Cities across the world are reeling from the direct impacts of deforestation and forest degradation. In neighborhoods with low tree cover, higher mortality rates from extreme heat are on the rise, disproportionately affecting poor and marginalized communities. Meanwhile, deforestation and other disturbances to the world’s forests emit an average of 8.1 billion metric tonnes of carbon dioxide every year, contributing to devastating climate impacts in cities across the world.

At the same time, cities are the ones shaping forests around the world. Although cities cover only a small proportion of the earth’s surface area, their carbon footprints are large and extend far beyond their limits. Ongoing consumption of globally traded agricultural commodities – the vast majority of which are consumed by urban residents – is the leading driver of tropical deforestation. For example, 80 percent of permanent deforestation in South-East Asia is the result of land conversion to grow commodities such as oil palm.

The fates of cities and forests are deeply intertwined—which also offers us an opportunity to change course. Cities can redefine the role of nature within and outside of their boundaries. By taking action to protect, restore and sustainably manage forests at all scales, cities can tackle the global climate and biodiversity crises while promoting the well-being of their residents. The public policies and procurement practices of cities have enormous potential to support the rejuvenation of the world’s forests—with huge benefits in return.

Until now, there has been a lack of clarity on how forests directly benefit cities and their residents. This report synthesizes hundreds of research articles to characterize the wealth of benefits that forests offer to cities in terms of human well-being, water security, climate mitigation, and biodiversity. The report evaluates the full range of benefits that cities receive from forests, whether they are inside, nearby, or far away from their boundaries, highlighting innovative examples from cities who are already leading the way. For example, the Green Cadaster in Skopje, North Macedonia offers a comprehensive map and catalog of every single tree and shrub in all public green zones within the city, making it easier for city officials to manage and track the benefits of green spaces. In Quito, Ecuador, a multi-stakeholder water fund known as FONAG has protected and restored over 40,000 hectares of forests with the support of over 400 local families. These are shining innovations and examples that decision makers across the world can learn from and seek to replicate in their own cities.

The report also echoes the Cities4Forests Call to Action on Forests and Climate that more than 50 mayors issued in 2021, calling for accelerated national and subnational action to support forests. As the first of its kind, this report provides city leaders with a new authoritative source to develop and expedite their efforts to protect forests worldwide.

As centers of political, economic, and cultural clout, city leaders have an increasingly important role to play. Mayoral voices are not yet tapped to their full potential in support of the world’s forests. This needs to change, and soon. After all, the battle on climate change will be won or lost in cities. We cannot afford to lose any more time. By 2050, an estimated 70 percent of the world’s population will live in cities. City leaders must act decisively in order to secure a green future for their growing populations and reap the benefits of a world with healthy forests.

Ani Dasgupta

President & CEO World Resources Institute

Better forests make for better cities

In the coming decade, city mayors and managers will face unprecedented demands from growing urban populations. Rapid urbanization and environmental changes are putting new pressures on burgeoning cities. City leaders are charged with providing urban residents with a safe place to live and work, environments that promote good health, clean and reliable freshwater, and protection from natural disasters. They will need to step up their climate action and meet other sustainability commitments—all of which are rising on political and media agendas. At the same time, city leaders will need to juggle these demands amidst dynamic conditions, often with tight financial resources.

Nature-based solutions¹ (NBS)—such as trees and forests—can help cities meet many of these needs. A growing body of scientific evidence shows that conserving, restoring, and sustainably managing forests can provide robust, low-cost infrastructure solutions to complement other traditionally built infrastructure. Cities around the world are responding to this evidence, increasingly using forests to address their challenges and meet the aspirations of residents.

Forests inside, near, and far away from cities (Figure ES-1) can help cities both meet their needs and contribute to commitments to act on global challenges:

• Inner forests include street trees, trees and forests on private property, patches of native woodland, forested ravines and corridors, and so forth, found within city boundaries. Inner forests can improve air quality, reduce the heat island effect (leading to lower energy use and energy bills), reduce stormwater runoff and urban flooding, provide access to nature and respite from the built environment, and support human health and wildlife.
• Nearby forests are trees, woodlands, and forests in the watersheds surrounding cities. They contribute to cleaner air in cities, support stable supplies of clean drinking water, reduce flooding, provide wildlife habitat, and offer space for recreation.
• Faraway forests are substantial, intact, and remote forests that are most often located far outside a city’s boundary. These forests—particularly those in the tropics—sequester large amounts of carbon, generate reliable rains for cities and the world’s agriculture belts, provide a wealth of products used by cities every day (including medicines, food, and building materials), and host the majority of the world’s land-based biodiversity.

Figure ES-1 | Inner, Nearby, and Faraway Forest Benefits

Note: Forests at three levels provide benefits to cities and contribute to the achievement of the UN Sustainable Development Goals.

Source: Cities4Forests n.d.a.

Forests are particularly effective at providing cities and their residents with four benefits: human health and well-being, a clean and reliable water supply, climate regulation, and biodiversity conservation. Better Forests, Better Cities evaluates the evidence base to show how and where these benefits are delivered by forests and, in unique circumstances, when and where they are not. This report presents a review of hundreds of synthesis papers, original research papers, and key reports. Collectively, this research shows how different forest types at different levels can deliver a diverse suite of benefits to cities.

Findings from the Scientific Literature

Health and Well-Being

Cities afford their inhabitants many benefits, but they also create conditions that can have negative impacts on health and well-being (Kuddus et al. 2020). Forests and trees, particularly in the inner forest, can improve the health and well-being of urban residents by these actions:

• Reducing extreme heat. The urban heat island effect—in which urban areas experience higher temperatures than their rural surroundings—presents a number of risks to human health. These include increased risk of heat-related deaths, increased concentrations of urban smog and ground-level ozone, spikes in energy and water demand, and power outages (Heaviside et al. 2017). Urban trees and forests can mitigate the urban heat island effect by providing shade and cooling the air via evapotranspiration. These processes reduce both the risk of heat-related illness or death and increase the livability of cities (Bowler et al. 2010a; Mohajerani et al. 2017; Wolf et al. 2020).
• Enhancing urban air quality. Ambient air pollution threatens the well-being of most urban residents. Nine out of 10 people breathe polluted air worldwide, leading to about 4.2 million deaths globally. Low- and middle-income countries are disproportionately affected (WHO 2016). Reducing emissions from the source is key, but carefully planned and managed inner forests can further improve air quality by removing and dispersing air pollutants (Nowak et al. 2014; Kumar et al. 2019; Hewitt et al. 2020).
• Promoting mental and physical health. Living in cities can take a toll on mental and physical health. Pollutants, being sedentary, and living close to other people can increase the prevalence of many kinds of diseases (Bai et al. 2012; Ventriglio et al. 2021). Forests and trees reduce noise, pollution, and other stressful conditions, and they provide opportunities for rest, relaxation, and recreation in nature (Hartig et al. 2014; Kuo 2015; Bratman et al. 2019; Wolf et al. 2020). Preventing deforestation and degradation of biodiverse forests outside cities may also reduce the spillover of infectious diseases, including novel viruses, from animal hosts to humans (Alimi et al. 2021).
• Creating safe, walkable streets. Cities around the world are working to increase biking and walking as ways to travel. Trees along streets and urban green spaces encourage active transport, providing shade, reducing localized air pollution, and making streets and pathways more beautiful and pleasurable (Wolf et al. 2020).
• Supporting community connections. Forests and other green spaces can build cohesion among urban residents by providing places for communities to gather, enhancing a “sense of place,” and creating space for spirituality and reflection (Wolf et al. 2014; Jennings et al. 2016). Inner and nearby forests are desirable locations for social gatherings, recreation, tourism, and spiritual practice and contemplation (Kuo 2015; O’Brien et al. 2017; Irvine and Herrett 2018; Ngulani and Shackleton 2019).
• Reducing inequity and empowering residents. Social and economic inequality is a challenge facing most cities. Lower levels of urban tree canopy cover have been associated with relatively low-income and marginalized populations in some cities (Schwarz et al. 2015; Jennings et al. 2016; Gerrish and Watkins 2018; Watkins and Gerrish 2018). Unequal tree distribution can translate into unequal distribution of the important human health and well-being benefits trees provide (Jennings and Johnson Gaither 2015; Braubach et al. 2017). Engaging communities to plan and integrate more trees and natural areas into neighborhoods with marginalized and low-income residents can help to address systemic inequalities in urban areas (Wolch et al. 2014; Kondo et al. 2015; Jelks et al. 2021). Meaningful community engagement and leadership is essential to realize these benefits.
• Providing food, medicine, and raw materials. Although city residents rely heavily on imported goods sold in formal markets (e.g., stores), inner and nearby forests can help improve food access, especially for lower-income or marginalized groups in cities. These forests can provide food, medicines, and raw materials for subsistence or can provide income (Pramova et al. 2012; Shackleton et al. 2015).
• Enhancing economic well-being. Inner forests can provide multiple economic benefits to cities and city residents (Nesbitt et al. 2017). Trees can increase property values for residents and associated property tax revenues for municipal governments (Roy et al. 2012). They can serve as a form of “green infrastructure” that can lower the costs of stormwater management, reduce flooding risks, lower energy costs, and provide other cost-saving measures.

Water

Forests and trees at all three levels can be a cost-effective way to help improve and stabilize city water resources. Many cities struggle to provide ample clean water (water is “too dirty”), address flooding and erosion (there is “too much” water), plan for droughts (there is “too little” water), and deal with new levels of inconsistency in once-reliable rain patterns (water is “too erratic”).

Too dirty: Many cities find it difficult to provide residents with a reliable supply of clean drinking water. Contaminated drinking water causes severe health issues in many regions, and water treatment facilities can be costly to establish and maintain. Forests in watersheds can prevent soil erosion and filter sediment and pollutants (Kuehler et al. 2017), keeping surface waters and aquifers cleaner and reducing costs to cities. For example, recent analysis finds that upstream forest protection and restoration can reduce costs for water utilities in the world’s 534 largest cities collectively by US$890 million per year (McDonald and Shemie 2014). Mature native forests provide these benefits more reliably than plantations.

Too much: By 2030, riverine flooding will impact around 130 million people and $535 billion in urban property, and coastal flooding will impact another 15 million people and $177 billion in urban property.² Forests—especially nearby forests—can prevent or reduce the severity of flooding. Forests intercept and store rainwater, reducing stormwater runoff. They improve the ability of soil to hold water, increasing both infiltration (entry) and percolation (downward movement) of rainwater (Berland et al. 2017; Kuehler et al. 2017). They increase the amount of water returned to the atmosphere by evapotranspiration. And they can store excess runoff, holding and slowing the release of water much like a sponge. Forested watersheds (near cities) regulate water flows and help prevent flooding and landslides. Trees and other vegetation in bioretention areas, green roofs, and bioswales can also complement traditional, engineered water infrastructure solutions for stormwater management in urban areas.

Too little: Water scarcity can be caused by drought, groundwater depletion, or reduced river flows. Many cities around the world—especially in arid regions—face seasonal or year-round issues with water supply. The “Day Zero” drought-induced water crisis in Cape Town of 2017–18 drew worldwide attention to the risks of too little water: thousands of people lost their jobs, food security decreased, and a political crisis ensued. Preventing deforestation and restoring forests can help sustain water availability (Brauman et al. 2007; Filoso et al. 2017; van Dijk and Keenan 2007; Zhang et al. 2017) by increasing the infiltration capacity of soils, which promotes groundwater recharge, although benefits may lag in reforested areas and water yields may decline initially in the years immediately following restoration or reforestation (Filoso et al. 2017). Forests also affect rainfall patterns at regional and even global levels. By capturing and recycling precipitation, evapotranspiration sends water into the atmosphere, creating “flying rivers” that transport water to fall as rain in downwind regions far from the forest.

Too erratic: Urban residents are vulnerable to increasingly erratic weather patterns, including longer and more intense droughts and heavy rainfall, linked to climate change. Variability and unpredictability in precipitation and water supply create additional challenges for municipal leaders, such as providing a reliable water supply to residents or preparing for unpredictable water highs and lows. Because of their role in the global water cycle, forests can help reduce this variability. Forests, especially large tracts of intact forests and rain forests, recharge atmospheric water supplies and thereby influence rainfall patterns hundreds to thousands of miles away. Forests also can reduce local water variability by enabling a slow release of water over time. Conserving and restoring forests are important strategies for stabilizing precipitation levels and groundwater availability in a changing climate (Melo et al. 2021).

Climate

The effects of climate change—including heat waves, flooding, rising sea levels, and droughts—threaten both the well-being of urban residents and the costs of operating a city. Not surprisingly, urban residents’ concerns about climate change are growing rapidly. Forests are good for both climate change adaptation and mitigation, and some of the adaptation benefits (for example, flooding reduction) have previously been mentioned. This section focuses on how forests can mitigate climate change. Cities around the world are committing to bold action to reduce their greenhouse gas (GHG) emissions and tackle climate change. C40 Cities Climate Leadership Group (an international network of megacities that have committed to take action on climate change), ICLEI—Local Governments for Sustainability, and the Carbon Neutral Cities Alliance are all examples of city networks committed to reducing GHG emissions. The first important step is to reduce GHG emissions from sources within cities and from city consumption, but forests can help cities go further.

Forests and trees in cities can reduce energy-related GHG emissions by modulating temperature. Inner forests reduce extreme heat in summer and shade buildings (Mullaney et al. 2015; Ko 2018). These trees can help residents and businesses adapt to rising temperatures while simultaneously reducing emissions generated by cooling and heating buildings with fossil fuels. In the United States alone, urban forests reduce electricity use by 38.8 million megawatt-hours at a savings of $4.7 billion annually, with reductions in heating use estimated at 246 million British thermal units at a savings of $3.1 billion annually, and avoided emissions valued at $3.9 billion annually (Nowak et al. 2017).

Inner forests provide modest opportunities to sequester and store carbon in wood and soils (Nowak et al. 2002; Roy et al. 2012; Nowak and Greenfield 2018b). However, total carbon storage is limited by the cost and availability of space in cities, and both total storage and sequestration rates in urban forests vary with climatic and other biophysical factors (Nowak et al. 2013; Dobbs et al. 2014; Chen 2015). Cities with favorable growing seasons, ample water supplies for vegetation, and robust urban forest management programs tend to store more carbon. Although inner forests do store carbon (and provide many cobenefits), planting trees and expanding the urban tree canopy will never be a sufficient way for cities to meaningfully compensate for their energy and transportation emissions. The number of trees that can fit within an urban area (and thus their stored carbon) is very small relative to a city’s annual carbon emissions (Pataki et al. 2011). Urban forests can only sequester a tiny fraction—often less than 1 percent—of overall city emissions. Urban forests can also be carbon neutral or carbon positive in some cases, meaning that they may emit as much or more carbon as they sequester. Throughout China, for example, the annual carbon sequestration of urban vegetation in 35 of its largest cities could offset only 0.33 percent of these cities’ total annual emissions (Chen 2015). Importantly and in all instances, urban forests will always sequester more carbon than they would if the forests were converted to other land uses.

Protecting and restoring faraway forests is critical to reduce emissions and mitigate global climate change. Often underappreciated by city climate action planners, faraway forests provide large-scale carbon sequestration for climate change mitigation. Forests, especially tropical forests, are large reservoirs of carbon that are released if the forest is cleared. But if forests are conserved, those stores are protected, and standing or restored forests continue to sequester even more carbon. Cities can play a big role in realizing this carbon opportunity and can help meet their own carbon reduction or neutrality commitments in the process. For instance, cities can lower their forest-carbon footprint by ensuring that the commodities they purchase for city infrastructure and operations—such as timber, paper, and food—come from deforestation-free supply chains or by reducing food loss and waste or shifting the diets of their residents towards more plant-based foods. Cities can partner with selected faraway forests that have a social or economic link to the city, offering programs that support the conservation and/or restoration of that faraway forest. Moreover, cities can financially support reductions in tropical forest-related emissions by participating in jurisdictional REDD+ (reducing emissions through deforestation and degradation, plus the sustainable management of forest and the conservation and enhancement of forest carbon stocks) programs verified by a credible standard.

Biodiversity

Biodiversity—global and local—provides many direct and indirect benefits to cities, and cities can play a key role in protecting biodiversity at regional and global levels. The biodiversity of plants, animals, fungi, and other life forms is declining rapidly because of human activities, both in and outside of cities (Tilman et al. 2017; Mazor et al. 2018). Maintaining—or even increasing—biodiversity in inner forests is increasingly appearing on municipal agendas (Brende and Duque 2021). Yet municipal policies and practices can support forest biodiversity in nearby and faraway forests too. Supporting forest-based biodiversity is important to cities for a number of reasons, including providing direct benefits and supporting many of the benefits in the other three sections of this report.

• Biodiverse forests often provide more—and more reliable—goods and services (Fischer et al. 2006; Flynn et al. 2011; Cardinale et al. 2012; Oliver et al. 2015). To provide the myriad benefits of trees to urban residents, forests must be able to persist and recover from changes in the environment, including storms, droughts, and a changing climate. High levels of biodiversity can serve as biological “insurance”—when an ecosystem has many species fulfilling similar roles, it can continue to function even if some of those organisms are lost or if a disease (e.g., Dutch elm disease; chestnut blight) wipes out an entire species from an area (Yachi and Loreau 1999; Brandon 2014).
• Biodiverse forests store more carbon, more reliably. Undisturbed native forests sequester more carbon and store it for longer than degraded forest or monoculture plantations (Holl and Brancalion 2020; Watson et al. 2020). Biodiverse forests have higher resilience to fluctuations in climate, pest outbreaks, and diseases than tree monocultures. This higher resilience makes them a more reliable carbon sink (Turner et al. 2009; Brandon 2014; Seddon et al. 2019).
• Biodiverse forests protect watersheds. Native, biodiverse forests in watersheds are more effective than planted monocultures at supplying water resources to downstream cities (Alvarez-Garreton et al. 2019; Bonnesoeur et al. 2019; Yu et al. 2019). This is due to the structure, impact on soils, and greater resilience of native forests creating better conditions for storing and filtering water.
• Biodiversity provides blueprints for new medicines. Biodiversity within forests has provided compounds and genetic material for making antibiotics, anticancer agents, anti-inflammatory compounds, and analgesics used around the world (Chivian and Bernstein 2010; Sen and Samanta 2014). In developing countries, 70–95 percent of the population, including those living in cities, rely on traditional remedies such as herbal medicines derived from forests for primary care (Robinson and Zhang 2011).
• Biodiverse forests support urban food supplies (Krishnan et al. 2020). Thirty-five percent of food produced globally comes from 800 plants that rely on pollination by insects and other animals (Klein et al. 2007). Forests provide critical habitat for many of these pollinators (Öckinger and Smith 2007; Nicholls and Altieri 2013; Bailey et al. 2014; Hipólito et al. 2019).
• Protecting biodiverse forests can reduce risks of zoonotic and vector-borne diseases. Deforestation, forest degradation, and the associated wildlife trade has been linked with the spread of diseases that jump from animals to humans—which cause immense health and economic damages (Wolfe et al. 2007; Karesh et al. 2012; Jones et al. 2013; Borremans et al. 2019). Examples include the Ebola virus, yellow fever, malaria, Zika virus, and coronaviruses (Guerra et al. 2006; Wilcox and Ellis 2006; Karjalainen et al. 2010; Monath and Vasconcelos 2015; Olivero et al. 2017). Evidence suggests that conserving tropical forests and sustaining their high levels of biodiversity can decrease transmission of some infectious diseases (Evans et al. 2020; UNEP 2020).
• Access to biodiverse nature in cities can provide more reliable and richer benefits to residents, including an important list of mental and restorative health benefits (Fuller et al. 2007; Lai et al. 2018; Wood et al. 2018; Marselle et al. 2019; Ngheim et al. 2021). Urban trees and forests are one of the main ways urban residents experience nature (Pregitzer et al. 2019). Biodiversity in the urban forest also contributes to the distinctive character of cities around the world (Hausmann et al. 2016).
• Inner forests can house high biodiversity. Urban forests can be highly biodiverse and can serve as corridors for some species. But they also tend to have more invasive species, “generalist” species, and fewer endemics (species with very limited ranges) than rural forests in the same habitat type (Concepción et al. 2015; Ducatez et al. 2018; Borges et al. 2021). Managing urban forests for biodiversity can provide access to nature within cities and create more resilient urban forests, essential for delivering other forest benefits.
• Tropical forests hold most—up to 90 percent—of the planet’s terrestrial biodiversity and thus are essential to urban well-being (Wilson 1988; Reid and Miller 1989; WRI et al. 1992). Tropical forests continue to be lost at alarming rates.

Cities around the world are responsible for the lion’s share of deforestation via their consumption. This also puts them in a strong position to improve their own biodiversity impacts through local policies that reduce negative impacts on tropical forests.

Right Trees, Right Place

Forests can provide the many benefits described in this report. But sometimes, the wrong trees in the wrong places can result in unintended and negative consequences. For example, monocultures of trees along city streets are vulnerable to pest and disease outbreaks (such as Dutch elm disease and the emerald ash borer). Our research found that some tree species emit volatile organic compounds and bioparticles (such as pollen) that can worsen urban air quality. In some situations, trees planted in urban street “canyons” formed by tall buildings can trap polluted air near the ground, preventing air currents from dispersing the pollution. Invasive tree species planted in cities can reduce native biodiversity and can even damage neighboring forests if they spread beyond city limits. Some species of tree also fail to thrive in harsh urban environments where air pollution, wind, and harsh temperatures can damage trees. In nearby and faraway forests, monoculture tree plantations can decrease biodiversity and sometimes even reduce carbon stores, especially if they replace native forests. In certain circumstances, upstream tree planting or forest restoration will decrease downstream water availability. For example, in Quito, Ecuador, millions of eucalyptus trees planted throughout the city and in nearby watersheds now diminish urban biodiversity, create forest fire risks, and can lead to soil erosion (compared to native tree species). Thus, ensuring the “right trees” are in the “right place” is critical for receiving the full benefits of forests at all levels.

Recommendations for Policy and Action

What can city leaders do to realize the myriad benefits forests provide to their cities and residents? Our analysis has identified actions cities can take, and our synthesis of the literature and interviews categorized these under five thematic categories:

1. 
   Measurement and monitoring
2. 
   Planning
3. 
   Partnerships
4. 
   Finance
5. 
   Markets

The following are a suite of “no regrets” measures that allow a city to take immediate action to capture the potential of inner, nearby, and faraway forests to help meet their goals (Figure ES-2). While not exhaustive, they provide directions towards tangible actions. Underpinning these measures are a set of guiding principles that apply to all recommendations (Box ES-1). Suggested policy actions are divided by level—inner, nearby, and faraway forests—and the thematic category that each action addresses.

Recommendations for Inner Forests: Urban Trees, Parks, Green Infrastructure, and Natural Areas

The following options can help city leaders advance the quantity and quality of inner forests—and thus the benefits those forests provide to urban residents. Since most inner forests fall within a city’s jurisdiction, cities often have full authority to pursue these recommendations.

Measurement and Monitoring: Inner Forests

• Map, inventory, and monitor your city’s urban forest. Develop an urban tree cover baseline and land cover map as a first step towards planning and monitoring urban forests. Include an inventory of large, old, and culturally relevant trees. Evaluate key urban environmental challenges that could be improved through better forest management, such as heat islands, urban flooding, and inequities in access to green space (WRI Mexico 2016; Singapore-ETH Centre n.d.).
• Quantify the benefits of urban trees, especially iconic and mature ones. Such an analysis is critical for informing policies and investments in urban trees and can garner political and resident support. For example, following its success in the United States, i-Tree Eco³—an online tool developed by the U.S. Forest Service to quantify and value ecosystem services provided by trees—was recently adapted, translated, and launched for Mexican cities, allowing cities across Mexico to quantify the extent and composition of urban forests and calculate ecosystem services and monetary values.
• Align forest monitoring metrics with city goals. Although canopy cover is often measured to assess urban forests, this single metric does not provide comprehensive information on all forest benefits. Use other metrics that improve forest function, such as forest types, species diversity, carbon density, proximity to residents, and distribution (Pregitzer et al. 2019).
• Articulate clear goals. These are a few examples:
  • Increase forest canopy by X percent. The appropriate canopy cover targets will depend on what is appropriate for local conditions (e.g., climate, natural tree canopy cover outside the city) and should be used with additional targets—such as species diversity or a mix of stand ages—to ensure forest diversity and health.
  • Ensure every resident has green space within a half mile of home. This addresses the increasing appetite of cities to achieve equitable access to green space for their residents.
  • Reduce heat island or stormwater threats by X percent. In the face of climate change, cities are increasingly looking to establish targets that address climate risks, such as flooding, drought, and heat

Planning: Inner Forests

• Develop an urban forest management plan. The plan should be scientifically informed, inclusively developed, and climate resilient. The plan should inform and be informed by other citywide plans, such as transportation, housing, land use, parks, and economic development.
• Designate land specifically for natural areas. These include parks, vacant lots, and along roadways. For example, the Miyawaki method—in which diverse plantings of native trees and shrubs are used to create “microforests”—has been used to improve local access to nature and increase urban biodiversity in many cities around the world (Nargi 2019). Be explicit about the use of these natural areas to promote community gathering and better access to nature for all residents.
• Create connectivity. Corridors of tree-covered green space can facilitate the spread of pollinators, support wildlife, alleviate stress, increase foot and bike commuting, and reduce exposure to pollution for residents. Successful examples of green corridor projects include the Medellín Green Corridors (UNEP 2019) and the Barcelona Green Corridor Network (O’Sullivan 2017).

Partnerships: Inner Forests

• Seek out organizations conducting innovative work on inner forests. For example, the Natural Areas Conservancy in New York City is a formalized partnership that focuses on maintaining and improving the city’s vast natural areas network, integrating the city’s needs with the conservation benefits these areas provide.⁴
• Cultivate interagency and cross-jurisdictional collaboration. Managing forests for multiple benefits spans different city agencies, including health, water, land use, transportation, economic development, climate, air pollution/quality, and parks/recreation. The Joint Benefits Authority⁵, which is being pioneered in San Francisco, is an example of a new mechanism that allows multiple departments within a city to jointly plan, implement, and finance projects to increase the quantity and quality of inner forests.

Finance: Inner Forests

• Explore diverse, long-term financing mechanisms to manage, protect, and expand urban forests. Innovative financing tools include the following:
  • Green bonds and climate bonds, which fund projects that have positive environmental and/or climate impacts through the use of proceeds or asset-linked bonds
  • Pay for performance environmental impact bonds (also known as pay for success bonds and social benefit bonds), which allow private investors to fund specific interventions and earn a return based on performance (i.e., paying for results rather than services)
  • Community-based public-private partnerships between local governments and private entities, which align the interests of public, private, and community stakeholders around common goals
  • Tree-planting funds from taxes and stormwater fees
  • Tree banks, which collect funds when trees are removed and their replacement value cannot be achieved and support replacements in other places throughout the city
  • Mitigation fees, which require that development activities mitigate their impacts by planting trees on sites where disturbance occurs or pay the equivalent fees into the city’s tree canopy conservation account
  • Integration of forests into compliance plans for environmental requirements
  • Incentives for city residents to support trees and forests through tax reductions

Markets: Inner Forests

• Develop wood waste reuse programs. Rather than disposing of wood from urban trees in landfills, municipalities can develop wood waste reuse programs. Dead trees can become timber for local industry and construction and a variety of other energy-saving products. These programs help defer costs, create employment, store carbon, and foster integrative thinking and charismatic sustainable policies centered on trees in cities.

Recommendations for Nearby Forests: Watershed and Recreation Areas around Cities

The following options can help city leaders advance the quantity and quality of their nearby forests—and thus the benefits those forests provide to urban residents. Since most nearby forests fall outside city agency jurisdiction, partnership, and collaboration with other government agencies (e.g., state, provincial, federal), landowners, and managers will be necessary for implementation.

Measurement and Monitoring: Nearby Forests

• Map peri-urban and watershed forests and identify where forests are being lost around the city. Understanding where forests are, where loss is occurring, where risk of loss from fire or land-use change are high, and where restoration opportunities exist is essential for planning engagement with nearby forests.
• Quantify the benefits of trees in areas around the city. This can help garner support from residents and partners to support watershed management for city water supply.

Planning: Nearby Forests

• Support the development of “nearby forest” management plans with measurable goals and success metrics. A city could provide resources, such as funding, administrative support, and staff participation, and promote collaborative planning between government jurisdictions.
• Articulate clear goals. These are a few examples:
  • Restore X hectares by 2030.
  • Remove invasive species from key watersheds.

Partnerships: Nearby Forests

• Articulate and amplify shared goals. Forming collaboratives between city agencies, other government agencies, and landowners can be an effective way to do this. For example, the city of Denver collaborates with the National Forest System and state agencies in the Forests to Faucets initiative⁶, which has the shared aim of reducing wildfire risks and improving watershed services across Colorado’s Front Range (CSU n.d.).

Finance: Nearby Forests

• Clarify that forest protection and management are eligible infrastructure expenses. Many existing funds for infrastructure have not clearly stated their ability or priority for funding NBS, such as forests. Explicitly making NBS eligible for funds can open new funding sources for forest protection and management.
• Make the economic and business case. A “Green-Gray Assessment”⁷ (Gray et al. 2019) assesses the costs and benefits of using green infrastructure (i.e., forests and trees) or green and gray infrastructure versus relying solely on traditional gray infrastructure for securing stable and clean water supplies.
• Establish upstream-downstream partnerships to finance watershed management. Identifying the downstream beneficiaries (e.g., water utility, beverage company) of forest watershed services is a key first step to securing performance-based arrangements with the upstream land managers. Types of financing mechanisms being pioneered by cities include green bonds, forest resilience bonds, water funds, and water utility rate surcharges.

Markets: Nearby Forests

• Implement a robust procurement policy for local, sustainably sourced wood. Sourcing wood from sustainably certified managed forests within a city’s “woodshed” can help keep forests from being converted to other land uses.
• Explore the role of carbon markets to finance forest conservation or restoration. King County in the U.S. state of Washington established the Forest Carbon Program⁸; it provides the opportunity for local companies to compensate a portion of their own carbon emissions and support healthy forests within the county (King County 2020).

Recommendations for Faraway Forests: Intact and Remote Forests, Especially in the Tropics

City leaders can advance the quantity and quality of faraway forests—and thus the benefits those forests provide to urban residents. Because faraway forests fall outside a city agency’s jurisdiction, partnership and collaboration with other governments and stakeholders will be necessary for implementing the following actions. Given the critical role of tropical forests in mitigating climate change and the current threats they face, cities should allocate special attention to conserving and restoring tropical forests.

Measurement and Monitoring: Faraway Forests

• Conduct an analysis of city consumption linked to tropical deforestation. Tools such as the Forest Footprint⁹ can estimate a city’s impact on tropical deforestation driven by urban consumption of commodities (e.g., beef, soybeans, timber) associated with tropical deforestation (Cities4Forests n.d.b).
• Identify and track local attitudes and initiatives towards promoting deforestation-free commodities. This can help gauge levels of political support a city may have in taking steps to drive deforestation-free commodity procurement policies.
• Articulate clear goals to guide action. This is an example:
  • X percent of tropical wood and forest-risk commodities will be sustainably procured by X date.

Planning: Faraway Forests

• Calculate and develop an action plan to reduce the consumption of forest-risk commodities and city-driven carbon dioxide emissions associated with deforestation. The Forest Footprint tool can help cities to identify the size of their forest impact and the key commodities driving deforestation, which can help them plan their mitigative actions.

Partnerships: Faraway Forests

• Establish a “partner forest.” A partner forest¹⁰ is a faraway (usually tropical) forest connected to a city through a meaningful and mutually beneficial exchange. The city supports the partner forest by directing its purchasing power towards a product or service that the forest provides (e.g., shade-grown coffee, climate benefits, eco-
tourism). The goal of a partner forest program is to visibly support a tropical forest that provides direct benefits to the city and raise awareness of those benefits among city residents (Cities4Forests n.d.c).
• Establish relationships with organizations involved in forest conservation, restoration, and sustainable management to help implement faraway forest programs. Instead of trying to develop in-house expertise, cities can partner with one or more nonprofit organizations with on-the-ground experience in the forests of interest to help scope, design, and implement a faraway forest program.
• Call on subnational and national governments as well as businesses and financiers to conserve, restore, and better manage tropical forests. Being home to the majority of voters in many countries, cities can flex their political muscle by being vocal with state and national government leaders about the importance of faraway forests for city resident well-being. If faraway forests are to remain, the voice of cities needs to be heard.
• Incentivize the use of responsibly sourced forest-risk products. For example, the UK city of Chester, led by the Chester Zoo and the local member of Parliament, worked to encourage local businesses to use and sell products with palm oil certified by the Roundtable on Sustainable Palm Oil. Chester was recently certified as the first sustainable palm oil city worldwide (Chester Zoo 2019).

Finance: Faraway Forests

• Compensate for urban emissions by funding tropical forest conservation. Cities will have difficulty reaching carbon neutrality by cutting their direct emissions alone. Financing tropical forest conservation and restoration, certified by credible jurisdictional REDD+ programs, may offer ways to compensate for remaining urban emissions. A “climate co-op” could be created where cities purchase high-quality forest carbon credits via the voluntary carbon market to finance long-term forest conservation with associated carbon benefits.
• Match conservation and restoration efforts in the city with conservation in faraway forests. For example, for every tree planted within the city, a city could support parallel restoration efforts in a tropical forest. The London Enfield Council woodland restoration project is developing such a partnership on restoration with the city of Port Moresby (Papua New Guinea).

Markets: Faraway Forests

• Establish ecotourism ventures to conserve and sustainably manage forests threatened by competing land-use pressures. Cities can support the implementation of community owned and operated sustainable tourism programs by promoting these amongst their residents to develop a steady clientele pipeline, thereby bolstering the efforts of regional governments to boost local economies while also conserving faraway forests (Fitzgerald n.d.).
• Initiate tropical forest-positive procurement policies and campaigns. Cities can implement policies that discourage purchasing commodities implicated in deforestation and provide incentives for purchasing better-sourced commodities (or alternatives with lower tropical forest impacts). Tropical timber, coffee, chocolate, soy, and beef are commodities that are especially amenable to this approach.

For all of these measures—for inner, nearby, and faraway forests—healthy communications and engagement with city residents will be important (Box ES-2).

Concluding Thoughts

Home to more than half of the world’s population, cities are growing in their size, power, and impact on the natural environment. They face pressing challenges to provide their residents with essential services, including healthy, livable neighborhoods, clean and reliable water, action on climate change, and access to nature and biodiversity. Cities can use trees and forests to help meet these challenges.

Within cities, trees and forests—inner forests—can reduce extreme temperatures, reduce stormwater runoff, promote mental health, and provide shared spaces for recreation and relaxation. Forests around cities—nearby forests—can improve water resources, provide many forest goods, and offer access to nature. And faraway forests around the world are key to mitigating climate change, conserving biodiversity, and maintaining global rainfall patterns. Cities have many options available to support forests at all three levels and make the best use of the benefits they provide. Forests can also help cities reduce operating costs and pay long-term dividends that often increase over time. The best time to plant a tree was fifty years ago. The second-best time is today.

City leaders around the world are working hard to meet the needs of ever-growing urban populations. By 2050, an estimated 70 percent of the world’s population will live in cities (UNSD n.d.). City leaders strive to provide their residents with a safe place to live and work and with access to resources and environments that promote good health. They seek to improve and sustain clean, reliable water supplies and provide protection from natural disasters. And cities are increasingly stepping up to take action on climate change mitigation and to meet other sustainability commitments. International agreements to combat climate change and conserve biodiversity, city-level commitments to reduce greenhouse gas (GHG) emissions, and the need for companies based in cities to reduce their carbon footprints all put pressure on cities to find cost-effective solutions to environmental challenges. At the same time, they juggle these demands in dynamic environments, often with tight financial resources.

At their disposal is a nature-based solution that can help cities meet many of these aspirations: forests and trees. Cities around the world are turning to nature-based solutions¹¹ (NBS) to address their challenges and meet their goals. Forests, in particular, are increasingly recognized as a cost-effective way to deliver multiple benefits. This report synthesizes the literature on how forests can deliver four key benefits¹² for cities and their residents:

• Health and well-being by creating habitable, healthy, and favorable living conditions for city residents
• Water by securing access to clean and reliable water supplies, both within cities and in the key agricultural regions that feed them
• Climate by contributing to climate change mitigation and its effects on millions of urban residents
• Biodiversity by protecting essential global biodiversity, which supports many of the systems people rely upon, such as pollinating crops, providing medicines, regulating climate, and underpinning many spiritual values

Benefits of Forests

Forests—both within and beyond city boundaries—provide benefits to cities and their residents. Our framework (Figure 1) divides forests into three levels—inner, nearby, and faraway—to show what the benefits are, how they differ depending on the location of the forest, and how cities can support forests to harness the greatest benefits. This framework was conceived by the founders of the Cities4Forests¹³ initiative, based on multiple projects and engagements with both forest and city landscapes.

• Inner forests include trees and forests growing along streets, in city parks, on private property, as remnant patches of native forests or woodland, and in urban coastal areas within cities. These inner forests can improve air quality, offset heat islands (leading to lower energy use and bills), reduce stormwater runoff and urban flooding, and support human health and wildlife.
• Nearby forests include forests, woodlands, and trees found in watersheds surrounding cities. They enhance urban air quality, regulate temperature, provide stable supplies of clean drinking water, reduce flooding, and offer opportunities for relaxation and recreation.
• Faraway forests are intact forests located beyond a city’s watershed. These forests, particularly those in the tropics, sequester large amounts of carbon, generate rain for cities and the world’s farm belts, provide a wealth of useful products, and host the majority of the world’s land-based biodiversity.

Figure 1 | Inner, Nearby, and Faraway Forest Benefits

Note: Inner, nearby, and faraway forests provide multiple benefits to cities, many of which are aligned with the UN Sustainable Development Goals.

Source: Cities4Forests n.d.a.

Threats to Forests

Across the globe, forests are under threat. During the decade 2010–19, global forest cover declined by an average of 4.7 million hectares (ha; 11.8 million acres) per year (FAO 2020).¹⁴ In 2019 alone, the world lost an area of tropical primary forest the size of a football pitch every six seconds (Weisse and Goldman 2020). In the world’s largest intact forests, deforestation and forest degradation are driven largely by agriculture, fires, and logging (Figure 2). Inside cities, pollutants, high temperatures, compacted soils, pests, and diseases create challenging conditions for trees to grow and survive. Urban tree cover has been decreasing at an average rate of 0.04 percent per year (Nowak and Greenfield 2020). In the United States alone, this loss represents about 36 million trees per year, equating to an estimated financial loss of US$96 million per year in benefits (Nowak and Greenfield 2018a). Urbanization often encroaches on woodlands surrounding cities, and an estimated 9 in 10 cities have lost significant amounts of natural land cover in their source watersheds to agriculture and development (McDonald et al. 2016).

Figure 2 | Tropical Deforestation Rates over Time

Source: WRI n.d.a.

Global deforestation is not evenly distributed; tropical forests are being cleared at much higher rates than those in temperate and boreal regions. Commercial production of globally traded agricultural commodities—such as soy, beef, and palm oil—is the leading driver of tropical deforestation (Curtis et al. 2018). In response to consumer demand from people—including city residents—thousands of miles away, tropical deforestation rates continue to rise. For the past several decades deforestation rates have been much lower in temperate and boreal regions, although in temperate areas many of these forests were cleared in the past (Currie and Bergen 2008). Forest loss in temperate and boreal regions is now mainly due to fire and harvesting for wood and paper products, and forests sometimes regrow after clearing (Figure 2; Curtis et al. 2018).

Cities suffer the costs. The impacts of deforestation and forest degradation always extend far beyond the cleared region. Cities experience poorer air quality, flooding, landslides, and more extreme weather events, to name a few, as a result of deforestation near and far. Deforestation decreases the benefits that cities receive from forests (Figure 1) with negative impacts on the physical, economic, and mental well-being of urban residents. In a world struggling to combat COVID-19, deforestation and forest degradation have been linked to increased incidence of vector-borne diseases such as malaria (Karjalainen et al. 2010) and the emergence of infectious zoonotic diseases such as coronaviruses (Afelt et al. 2018).

Opportunities for Cities

Cities play a major role in forest loss and degradation. Consumption in urban areas is directly responsible for about 75 percent of global carbon dioxide (CO₂) emissions and two-thirds of global energy use (Seto et al. 2014). And although cities cover only a small proportion of the earth’s surface, their footprints are large: as major “net importers,” cities depend heavily upon resource extraction and production beyond their boundaries (Weinzettel et al. 2013). A midsize city in North America, for example, is responsible for thousands of hectares of tropical deforestation per year via the goods it consumes.¹⁵

Cities—as places where people increasingly live and work—can make major contributions to addressing these issues. The public policies and procurement practices of cities—as well as the values, votes, and consumption patterns of residents—have enormous potential to support the conservation, restoration, and sustainable management of forests. Many cities already support forests, for example, through efforts to expand urban tree cover and parks. Some cities provide incentives to protect watersheds for their water supplies, and there is growing investment in forests as “green infrastructure.” Some cities are implementing procurement guidelines to reduce tropical deforestation driven by city consumption. But the potential to do more is immense. The Intergovernmental Panel on Climate Change’s (IPCC) Special Report on Climate Change (Jia et al. 2019) estimates that 11 percent of global carbon emissions come from land-use change—especially tropical deforestation. If tropical deforestation were a country, it would rank third only behind China and the United States in GHG emissions (Gibbs et al. 2018). Conserving, sustainably managing, and restoring forests and other ecosystems could reduce global GHG emissions by up to 30 percent and provide 23 percent of the cost-effective mitigation measures needed to prevent global temperatures from rising 2°C (Griscom et al. 2017; Wolosin and Harris 2018). Much more can be done to promote forests as a climate change solution (Seymour and Busch 2016).

About This Report and How to Use It

This report addresses two key questions: How and under what conditions do forests support cities? And what can cities do to support forests? To answer the first question, we rigorously research and explore four ways forests benefit cities¹⁶ and describe each in its own section (Table 1).

City representatives can use each section separately or all together, depending on their focus and objectives. For example, a city employee concerned with improving air quality could read Section 2 to learn more about how trees and forests can help. An official interested in making trees and green space a focus of the city agenda might read all four sections.

Sections 2–5 have a similar overall structure, with a “Background” section about the topic and its relevance for cities as well as a section that describes what forests do and—when data allows—quantifies their benefits. This latter section is formatted differently between sections to suit the specific subject. The “Caveats and Considerations” section highlights the nuances that are important for realizing the benefits, including when forests will not produce benefits, and what types of forests are most appropriate. This section helps urban decision-makers avoid unintended consequences and get the most from their investment in trees and forests. Collectively, this information can be used by city governments, city managers, other agencies, and groups such as nongovernmental organizations (NGOs) and community-based organizations that work with cities to rethink how they should engage with and use forests to achieve specific end goals.

The question “What can cities do to support forests in return?” is addressed in Section 6, which outlines what city leaders, managers, and other city stakeholders can do. The section includes recommendations on resident engagement and awareness, communications campaigns, public policies and procurement, finance, and more.

Methods

This report synthesizes the latest research on how inner, nearby, and faraway forests benefit cities and urban residents. It summarizes research findings gathered through several literature reviews, including several “reviews of reviews” (surveys of published review papers; e.g., van den Bosch and Sang [2017]), supplemented by reviews of primary literature and expert-recommended texts. Reviews covered four main topics: health and well-being, water, climate, and biodiversity. There is a geographical bias of the “reviews of reviews” methodology, which was limited to published documents written in English. We partially correct for this by including findings from relevant empirical papers and by including case studies from under-represented areas identified through reference lists and expert recommendations. Sections of the report, such as Section 6, are also partly based on conversations with city representatives, interviews with topical experts, and experiences from years of projects that World Resources Institute (WRI), Pilot Projects, and Cities4Forests have worked on.

There is no universally accepted definition of forest (Chazdon, Brancalion, et al. 2016), and different fields of study use the term in different ways. We include research on both trees and forests as well as on natural and planted forests, and we make distinctions where appropriate. We also include work on urban nature, green infrastructure, and green spaces more broadly when forest-specific studies are lacking. A more detailed methodology can be found in Appendix A.

Background

Living in cities provides numerous benefits, including access to economic and educational opportunities, shorter commutes, public services, and intercultural exchange. But urban living can have negative impacts on the mental and physical health of residents. Exposure to air pollution, chronic stressors such as noise pollution, sedentary lifestyles, increased risk of communicable disease in crowded conditions, and extreme temperatures in the built environment can erode overall health and quality of life—and can sometimes be deadly (Bai et al. 2012; Kuddus et al. 2020). Climate change threatens to amplify impacts through higher temperatures, aberrant rainfall, and, for coastal cities, rising sea levels (Revi et al. 2014).

As they strive to create healthier cities, city leaders can embrace sustainably managed inner or “urban” forests as an NBS. When trees are integrated into the urban landscape in socially and ecologically appropriate ways, cities can become more livable and vibrant spaces. Evidence suggests that, unlike many issue-specific municipal investments, the “urban forest” can generate a diverse suite of benefits at the same time—from cooler temperatures and air quality improvement to improved health and space for social interaction.

How forests relate to human well-being

In 1984, a pioneering study found that patients whose windows looked out upon a group of trees healed from surgery faster and needed fewer painkillers than those whose windows had no view of nature (Ulrich 1984). Since then, a rapidly expanding and compelling body of evidence—spanning disciplines as diverse as epidemiology, psychology, forestry, and geography—suggests that forests and nature play an important role in human health. Evidence also indicates that forests in and around cities may contribute to social and economic well-being because benefits accrue to individuals using forests to support their livelihoods, to property owners whose parcels increase in value, and to entire regions as forests support tourism or other industries.

Why context matters

Cities are immensely diverse in climate, culture, politics, language, and environmental contexts. As such, considering the local cultural, political, climatic, environmental, and socioeconomic contexts is important for successfully integrating trees and forests into city planning. The benefits that forests in cities provide will vary from city to city around the world.

Inner forests (and related green infrastructure) may not always provide the intended benefits, and they can sometimes present unintended risks (Hartig et al. 2014; Lõhmus and Balbus 2015). By understanding these risks and deliberately incorporating how to address them into the planning and decision-making processes, the potential for unintended negative outcomes can be minimized and the many positive benefits realized (Lõhmus and Balbus 2015; Wolf 2017). And by empowering communities to guide urban greening initiatives and stewardship of the inner forest, these living elements of urban infrastructure can help to diminish—rather than exacerbate—inequities among groups.

About This Section

Forests near and far support human health and well-being—socially, economically, and ecologically. In the following sections, we summarize the ways that inner and nearby forests affect the quality of life of city residents. Local forests provide many direct and indirect health benefits. This section thus focuses on inner forests that provide unique opportunities for leaders seeking to create healthy and habitable cities. Nearby and faraway forests also provide health benefits via water access and treatment, climate change mitigation, and biodiversity, which are addressed in the respective sections.

To explore these benefits, we synthesized statements and goals shared by many city leaders around the world into eight specific goals related to health and well-being:

1. Reducing extreme heat
2. Enhancing urban air quality
3. Promoting physical and mental health in city residents
4. Creating walkable, safe streets
5. Supporting community connections
6. Reducing urban environmental inequity
7. Ensuring provision of food, medicine, and raw materials
8. Enhancing economic well-being

Goal 1: Reducing Extreme Heat

Context

Cities suffer from the heat island effect. Most cities are dominated by buildings and pavement, with relatively little vegetation and green space, which contributes to “urban heat islands”—elevated temperatures in urban areas compared to their rural surroundings. Urban areas can be 2°C–4°C—and as much as 15°C—warmer than adjacent areas (Taha 1997; Heaviside et al. 2017; Mohajerani et al. 2017). The heat island effect presents a number of risks to human health and well-being, including the following:

• Increased risk of heat-related mortality and morbidity, especially during heat waves; high temperatures can cause heat stroke, dehydration, exacerbate existing diseases, and even cause death (Luber and McGeehin 2008); stifling heat may also interfere with worker productivity (Zander et al. 2015) and with learning and educational achievement (Park et al. 2020)
• Potential for negative effects on mental health, although more research is needed (Thompson et al. 2018)
• Spikes in energy demand (Li et al. 2019)
• Power outages due to high energy demand at midday, which can further affect resident safety, impair economic activity, and burden health and emergency services (WMO and WHO 2015)
• Degradation of environmental quality, such as increased concentrations of urban smog (Akbari et al. 2001), increased ground-level ozone (Luber and McGeehin 2008; Jacob and Winner 2009), and decreased water quality (Phelan et al. 2015; Heaviside et al. 2017)

Climate change will exacerbate these risks. Since the advent of the Industrial Revolution, the average temperature near Earth’s surface has increased about 1°C (1.8°F; IPCC 2018). The urban heat island effect magnifies the effects of climate change for cities, leading to higher temperatures than rural areas and more extreme heat waves (Estrada et al. 2017). Already, extreme heat in cities has been responsible for thousands of excess mortalities in recent decades (Heaviside et al. 2017). The 2003 European heat wave, for example, killed more than 70,000 people (Robine et al. 2008). Thousands in India and hundreds in Pakistan died as temperatures surpassed 45°C in 2015 (Masood et al. 2015; Sarath Chandran et al. 2017). In 2021, a lingering heat wave shattered records in western North America, spiking heat-related illnesses and killing hundreds, an event the World Weather Attribution initiative described as “virtually impossible without human-caused climate change” (WWA 2021). Records suggest July 2021 was the hottest month on record (NOAA 2021).

Some urban residents are more susceptible to these risks than others. In general, lower-income and marginalized communities are disproportionately exposed to the deleterious effects of heat islands (UN DESA 2020). Children, people above the age of 50, and those with preexisting health conditions are particularly vulnerable to heat-related illnesses (Kovats and Hajat 2008). Densely settled and lower-income communities often lack access to places to cool down, such as shaded green spaces and open areas (Harlan et al. 2006; Luber and McGeehin 2008). In addition, many low-income households lack insulation, air conditioning, and access to resources necessary to cope with extreme temperatures (Harlan et al. 2006; Ko 2018).

What roles can trees and forests play?

Trees in urban areas can mitigate the urban heat island effect, especially locally, by the following actions (Figure 3):

• Shading surfaces and people. Tree canopies intercept and reflect up to 90 percent of incoming solar radiation. Shade makes heat more tolerable and can protect people from excessive sun exposure during travel, work, or leisure (Nowak and Dwyer 2007). Trees that shade buildings can reduce surface temperatures in a wide variety of contexts (Wang et al. 2014); for example, surface temperatures were reduced by 11°C–25°C in Sacramento, California (Akbari et al. 1997); by 5°C–7°C in Akure, Nigeria (Morakinyo et al. 2013); and by 9°C in Melbourne, Australia (Berry et al. 2013). In Bangalore, India, streets with trees had local ambient air temperatures that were 5.6°C lower than streets without trees, and their surface temperatures were 27.5°C lower (Vailshery et al. 2013).
• Cooling the air via evapotranspiration. During the day, trees may create lower air temperatures by releasing water into the air as they photosynthesize (Bowler et al. 2010a; Säumel et al. 2016). As water vapor is released, it takes with it some of the ambient heat. Large trees with ample access to water may evaporate more than 100 liters of water in a single day, which dissipates about 70 kilowatt-hours of solar energy that would otherwise remain stored in the urban environment (Fath 2018).

Effects of cooling are most pronounced locally. A 2010 global meta-analysis found that parks were, on average, 0.94°C cooler during the day than surrounding urban areas, with greater benefits in larger parks and in those containing trees (Bowler et al. 2010a). A more recent review suggests large urban parks and green spaces (more than 10 ha)—especially those with mature trees—can reduce air and surface temperatures by 1°C–2°C (Aram et al. 2019). Some evidence shows that areas adjacent to green spaces also are cooler (Mohajerani et al. 2017), from a few hundred meters (Tyrväinen et al. 2005; Aram et al. 2019) to perhaps as much as a kilometer (Bowler et al. 2010a).

The urban forest can both reduce the risk of heat-related illness or death and increase perceived comfort for residents (Taha 1997; Tyrväinen et al. 2005; Salmond et al. 2016; Gunawardena et al. 2017; Wolf et al. 2020):

• Researchers estimate that in 97 U.S. cities alone, urban tree cover helps to avoid 245–346 premature deaths and 50,000 hospitalizations annually (McDonald et al. 2020).
• In Toronto, residents in neighborhoods with the lowest tree canopy cover (less than 5 percent) made 5 times as many heat-related emergency calls as residents in neighborhoods with more than 5 percent canopy cover and nearly 15 times as many emergency calls as residents in neighborhoods with more than 70 percent canopy cover (Graham et al. 2016).

Figure 3 | Localized Cooling Benefits from Trees through Shading and Evapotranspiration

Notes: Pavement and concrete in cities absorb energy from the sun and then radiate that energy out, heating the air in cities more than in the surrounding countryside. Urban trees provide shade, preventing pavement and concrete from heating up, and also cool the air by transpiring water. Trees can cool neighborhoods by up to 4 degrees Fahrenheit (McDonald et al. 2016).

Source: Authors. Adapted from McDonald et al. (2016).

Caveats and considerations

Urban forests may complement or be incorporated into other interventions to reduce the urban heat island effect. These interventions include permeable pavements and green roofs (Mohajerani et al. 2017).

Cooling by urban trees will be greatest in local areas, and forests may not provide net benefits in some situations, such as these:

• Trees and shrubs very close to buildings may prevent nighttime radiative cooling of buildings (Bowler et al. 2010a; Wang et al. 2014; Ko 2018).
• Tall trees can reduce wind speeds (Mohajerani et al. 2017). This can be a benefit in cold climates but can be a disadvantage in warm or humid climates (Ko 2018). At night, tree canopies can also reduce airflow and thus retain heat (Bowler et al. 2010a; Salmond et al. 2016).
• The microclimate-altering effects of urban trees and other vegetation are more pronounced in cities in warm and dry climates (Taha 1997).
• Because evapotranspiration increases humidity (Salmond et al. 2016), high levels of evapotranspiration may reduce comfort for urban dwellers in hot, humid climates, even as evapotranspiration lowers near-ground temperatures. However, the increase in humidity may be small compared to the reductions in temperature (Vailshery et al. 2013).

Some species provide more cooling benefits than others. Leaf area index, evapotranspiration rate, crown diameter, and the albedo of different tree species affect the cooling benefits they provide (Jim and Chen 2009; Bowler et al. 2010a; Smithers et al. 2018). Fast-growing, long-lived, and drought-tolerant native species of trees with relatively reflective surfaces are most likely to deliver cooling benefits (Smithers et al. 2018).

Goal 2: Enhancing Urban Air Quality

Context

Air pollution threatens the well-being of most urban dwellers. An estimated 9 out of 10 people breathe polluted air worldwide (WHO 2016). Responsible for approximately 4.2 million deaths globally in 2016 (WHO 2016), exposure to ambient air pollution is considered one of the greatest risk factors for global public health (Burnett et al. 2018). Exposure to air pollution disproportionately affects residents of low- and middle-income countries. It disproportionately affects lower-income and racial or ethnic minority residents, as documented in North America (Landrigan et al. 2018; Tessum et al. 2019; Nicolaou and Checkley 2021).

Air pollution needs to be addressed at the source (Baldauf and Nowak 2014; EPA 2019) because more pollutants are emitted than can reasonably be contained with mitigation measures. But eliminating air pollution is an intractable challenge to even the most well-resourced governments—especially pollution from nonpoint sources such as vehicles and woodsmoke/biomass burning from residences. Trees and other green infrastructure can help to remove these pollutants locally and/or be used to create barriers between pollutant sources and the people or organisms exposed (Baldauf and Nowak 2014; Hewitt et al. 2020; Wernecke and Pool 2022).

What roles can forests play?

Typically, urban forests reduce air pollution by around 1 percent at the city scale (Litschke and Kuttler 2008; Baldauf and Nowak 2014; Salmond et al. 2016; Sicard et al. 2018; Xing and Brimblecombe 2020). But even a modest reduction in pollution can be very valuable to cities. For example, in 2010, forests in the continental United States (both inside and outside of cities) removed an estimated 17.4 million tons of air pollutants such as particulate matter (PM), contributing to health benefits—including 850 avoided premature mortalities—worth an estimated $6.8 billion (Nowak et al. 2014). However, reducing pollutants further may require a large expansion in tree canopy cover (Litschke and Kuttler 2008; Nieuwenhuijsen et al. 2017). Models of the effects of urban trees on local air quality (i.e., site scale) suggest larger reductions are possible with proper planning and species selection (Pugh et al. 2012; Janhäll 2015; Abhijith et al. 2017; Barwise and Kumar 2020).

Forests and other vegetation can have positive or negative effects because they interact with urban air pollutants in several different ways. Urban trees alter pollutant concentrations by trapping pollutants or by redirecting airflow:

• Removing particles from the air (deposition) by either taking in gaseous pollutants or having particles settle on their surfaces (Beckett et al. 1998). Trees remove pollutants at faster rates than other types of vegetation (Fowler et al. 2004). Dense but porous vegetation serves as an ideal surface for deposition, superior to the comparatively smooth surfaces of buildings and roads.
• Dispersing pollutants (dilution) in the urban environment by altering airflow patterns and slowing wind (Abhijith et al. 2017). Dilution of highly polluted air with clean air from surrounding areas enhances urban air quality. Trees can help or hinder dilution: they may act as an obstacle, slowing wind speeds and reducing the exchange between clean and polluted air, suppressing pollutant dispersion (Säumel et al. 2016; Abhijith et al. 2017; Xing and Brimblecombe 2020) or as a source of turbulence that increases the exchange, based on characteristics of the built environment and on meteorological conditions.

But trees can also emit two types of particles that affect air quality:

• Biogenic volatile organic compounds (bVOCs) can act as precursors to pollutants such as ozone and secondary organic aerosols and can worsen air quality (Laothawornkitkul et al. 2009; Leung et al. 2011; Calfapietra et al. 2013; Cariñanos et al. 2017). Even healthy plants produce bVOCs (Smith 1981), but exposure to drought, pollutants, heat, and excessive sunlight, as well as physical injury or attacks by pests, may all induce the release of additional bVOCs (Laothawornkitkul et al. 2009; Calfapietra et al. 2013). Increases in global temperature may increase bVOC emissions further (Laothawornkitkul et al. 2009; Wang et al. 2014).
• Allergenic pollen can undermine health (Smith 1981; Beckett et al. 1998; Cariñanos and Casares-Porcel 2011; Säumel et al. 2016; Eisenman et al. 2019; Hewitt et al. 2020). Climate change and air pollution have led to the increased production of pollen in some tree species (Cariñanos and Casares-Porcel 2011). Allergies due to pollen can decrease the quality of life of urban dwellers, and allergen exposure has been linked to ill health conditions such as cardiovascular disease, pneumonia, and asthma (Curtis et al. 2006). Air pollutant exposure can even worsen the health impacts of pollen. When pollen grains (as airborne PM) interact with other air pollutants, they can be modified, enhancing their allergic potential as well as their penetration potential into the respiratory tract (Eisenman et al. 2019). Exposure to air pollutants can also exacerbate allergy symptoms (Jianan et al. 2007; Cariñanos and Casares-Porcel 2011).

How do trees interact with the built environment?

Trees in urban “street canyons” formed by tall buildings may trap polluted air near the ground level (Figure 4, top; Abhijith et al. 2017; Hewitt et al. 2020). In these street canyons, the movement of air is already restricted. Trees with canopies higher than 1–2 meters (m) may slow wind speeds and limit air pollutant dilution, increasing the concentration of various pollutants in urban canyons by as much as 20–96 percent (Abhijith et al. 2017). The aspect ratio (i.e., the height to width ratio of buildings to road) influences airflow in the canyon, as does vegetation density, tree spacing, and wind direction (Abhijith et al. 2017).

On the other hand, hedges and shrubs (around 1–2 m tall) in street canyons may provide an effective barrier between pedestrians and traffic emissions while permitting adequate dispersion of air (Figure 4; Janhäll 2015; Säumel et al. 2016; Abhijith et al. 2017). This is because low, permeable hedges create vortices that may carry air away from footpaths along roads and generally have positive effects on air quality at ground level (Abhijith et al. 2017).

Similarly, in open road conditions, trees and hedges can reduce the concentration of pollutants near highways by serving as barriers between pollution sources and human receptors (Figure 5; Abhijith et al. 2017; Xing and Brimblecombe 2020). Unlike vegetation in urban canyons, these barriers provide maximum benefits when the trees or hedges are tall (>0.5 m), thick (>10 m), and moderately porous (Baldauf 2017). Empirical studies have shown reductions in pollutant concentrations of 15–60 percent when trees and hedges are used as barriers along open roads (Abhijith et al. 2017).

Figure 4 | Air Pollution in Urban Street Canyons

Note: Urban trees can trap pollutants in urban street canyons (top) but can also serve as effective barriers between pollutants and people in some situations (bottom).

Source: Authors. Adapted from Trivedi et al. 2020.

Figure 5 | Trees as Effective Barriers between Pollutants and Pedestrians

Source: Authors. Adapted from Abhijith et al. (2017).

Strategic plantings of trees along roadsides could shield sensitive populations from exposure to PM and other pollutants, especially in areas with insufficient green space. Because deposition of pollutants on plant surfaces decreases with distance, trees should be planted as near as possible to the source of pollution (e.g., a road with automobile traffic) without blocking cleaner air from the atmosphere from entering the area (Litschke and Kuttler 2008; Leung et al. 2011; Janhäll 2015).

Caveats and considerations

As a result of the interactions, without adequate planning, the net effect of the inner forest on air quality in any given local area may be neutral or negative (Litschke and Kuttler 2008; Leung et al. 2011; Baldauf and Nowak 2014; Salmond et al. 2016; Sicard et al. 2018; Eisenman et al. 2019; Xing and Brimblecombe 2020).

When it comes to enhancing air quality, tree characteristics matter. Different trees remove different amounts of pollutant particles, depending on the following:

• Leaf texture (e.g., waxy, hairy) and surface area (Janhäll 2015). For example, leaves with many tiny hairs may capture more pollutants.
• Growth form. Shrubs (i.e., woody plants with many stems) remove more PM than trees, but both remove more PM than other types of plants, such as grasses (Cai et al. 2017). However, if the vegetation is too dense, it can become a barrier forcing air to move over instead of filtering through.
• Growth strategy. Evergreen coniferous species (e.g., pine) typically remove more pollutants and dust than deciduous species (e.g., sycamore or maple) because the tiny needle-like leaves of many coniferous species create an effective filter (Janhäll 2015). Evergreen species also bear leaves throughout the entire year and can thus intercept pollutants year-round (Cavanagh and Clemons 2006; Litschke and Kuttler 2008).

Adapting strategies to site characteristics and local context are important for good outcomes (Hewitt et al. 2020). A slew of factors in the built and natural environment affects whether trees will have a positive, negative, or neutral effect on air quality, including airflow patterns, wind speed, building height and density, local humidity, temperature, and proximity to and type of pollutant source, among other factors (Cavanagh and Clemons 2006; Litschke and Kuttler 2008; Elmqvist et al. 2015; Salmond et al. 2016; Cai et al. 2017; Kumar et al. 2019; Xing and Brimblecombe 2020).

Using low-emitting species can support air quality goals in urban areas by reducing bVOCs and pollen (Cariñanos and Casares-Porcel 2011; Calfapietra et al. 2013). Municipalities frequently overlook species selection during large-scale tree-planting projects (Churkina et al. 2015). One study estimated that selecting the low-bVOC-emitting tree species over high-emitting species in a large-scale tree-planting initiative in Denver would be equivalent to avoiding emissions from nearly 500,000 cars from inner-city traffic (Curtis et al. 2014).

More research is needed on how best to use trees to reduce air pollution in cities (Janhäll 2015; Abhijith et al. 2017; Eisenman et al. 2019; Kumar et al. 2019; Hewitt et al. 2020). In particular, research that explores the effects on dilution, empirically validates models, and reports on effects at multiple spatial scales is needed (Beckett et al. 1998; Janhäll 2015; Salmond et al. 2016; Xing and Brimblecombe 2020). Urban vegetation cannot substitute for source emissions reductions but can improve local conditions and lead to better health outcomes for residents.

Goal 3: Promoting Physical and Mental Health in City Residents

Context

Living in cities presents health risks (Bai et al. 2012; Kuddus et al. 2020). As a result of heightened exposure to air, light, and noise pollution and decreased exposure to sunlight and key microorganisms, urban dwellers may be more vulnerable to noncommunicable, immune, and respiratory diseases and infections (Flies et al. 2019). Urban lifestyles often permit fewer opportunities for physical activity, time in nature, and spaces for social connection with neighbors (Frumkin 2002).

Mental health can also be affected by the social, economic, and environmental conditions of the city landscape. Urban living can increase the risk of developing some mental illnesses and disorders (Peen et al. 2010; Lecic-Tosevski 2019; Ventriglio et al. 2019). Abundant sensory stimuli and high population densities in cities can create stress, with few opportunities for coping. Stress manifests in both the brain and the body (McEwen 2008) and is a factor in illnesses ranging from depression to cardiovascular disease (Cohen et al. 2007).

Many of the environmental hazards of cities—such as exposure to air pollution, unsafe drinking water, or extreme temperatures—disproportionately affect lower-income communities and marginalized residents (Frumkin 2002; Kondo et al. 2015). Creating healthier cities will require interventions to reduce disparities in access to health care, increase availability of safe housing, and further improve sanitation (Dye 2008). But the urban forest also serves as a dispersed and relatively low-cost element of public health infrastructure.

What roles can forests and green spaces play?

Natural environments can reduce stress (Case Study 1; Hartig et al. 2014; McCormick 2017; Nesbitt et al. 2017; Kondo et al. 2018; Summers and Vivian 2018; Bratman et al. 2019). Exposure to urban forests and other elements of nature may reduce risks related to chronic stress by the following actions:

• Providing opportunities for restoration (i.e., recovery) of a person’s adaptive capacity to cope with stressful life events or exposure to environmental stressors (Hartig et al. 2014; Bowler et al. 2010b).
• Dampening the effect of urban stressors. Noise, for instance, is both a nuisance and an environmental stressor that can interfere with communication, alter behavior, and impair work performance (Stansfeld and Matheson 2003). The foliage of urban forests can create a physical barrier that absorbs the energy of sound waves and reduces noise overall (Nowak and Dwyer 2007; Dzhambov and Dimitrova 2014; Wang et al. 2014; Säumel et al. 2016).

Exposure to nature—including forests and urban green spaces—is associated with better mental health and psychological well-being, including

• improved mood, perceived well-being, sleep, and ability to focus (Bratman et al. 2019); and
• reduced risk of some psychological disorders (Bratman et al. 2019) and better mental health outcomes (Wolf et al. 2020). For example, the presence of urban green spaces or residential greenness have been linked to lower anxiety and depression (see Braubach et al. [2017] or Vanaken and Danckaerts [2018]).

Exposure to forests and nature may benefit children’s mental development. A growing body of research shows that regular access to nature helps children thrive and is important for their mental health. Access to forests and nature has been found to improve cognitive functioning (Hartig et al. 2014; Jennings et al. 2016; McCormick 2017; Kondo et al. 2018) and reduce behavioral difficulties (Summers and Vivian 2018; Vanaken and Danckaerts 2018). Increased exposure to natural settings and outdoor activities in green spaces also may reduce attention-deficit/hyperactivity disorder (Braubach et al. 2017; Nesbitt et al. 2017; Summers and Vivian 2018; Vanaken and Danckaerts 2018), improve attention capacity (Tzoulas et al. 2007), enhance creative development (Bratman et al. 2019), and improve academic performance (Jennings et al. 2016; Bratman et al. 2019). For example, a study of more than 3,500 school-age children in London found that exposure to woodland was associated with higher cognitive development scores and lower risks of behavioral and emotional problems, even after controlling for other variables (Maes et al. 2021).

Exposure to green space, tree canopies, and urban nature is associated with better physical health (Case Study 1). Examples include the following:

• Reduced risk of noncommunicable diseases, including cardiovascular disease (Nieuwenhuijsen 2018; Wolf et al. 2020) and type II diabetes mellitus (den Braver et al. 2018; Twohig-Bennett and Jones 2018)
• Reduced indicators for stress and disease, such as salivary stress hormones, heart rate, and blood pressure (Meyer and Bürger-Arnd 2014; Hansen et al. 2017; Twohig-Bennett and Jones 2018; Wolf et al. 2020); forest bathing, in particular, seems to have positive effects on physiological states and immune activity (Case Study 1)
• Lower body mass index (Lachowycz and Jones 2011; Wolf et al. 2020), a predictor of other health outcomes
• Improved pregnancy and birth outcomes (Dzhambov et al. 2014; Braubach et al. 2017; Nesbitt et al. 2017; Twohig-Bennett and Jones 2018; Kloog 2019)
• Reduced risk of premature death; most evidence supports a significant inverse relationship between premature mortality and residential greenness (Gascon et al. 2016; Twohig-Bennett and Jones 2018; Rojas-Rueda et al. 2019)

Exposure to forests and nature can improve people’s immune systems (Kuo 2015; Shanahan et al. 2015; Braubach et al. 2017). Being exposed to a diverse array of microorganisms—to which humans were exposed for much of our evolutionary history—may stimulate the immune system and enhance its ability to distinguish between beneficial and harmful bacteria, which can improve health outcomes, including autoimmune disorders, allergies, depression, or cancer (Rook 2013; Kuo 2015; Sandifer et al. 2015; von Hertzen et al. 2015; Lai et al. 2019). These microorganisms are accessed in forests and nature.

Preventing deforestation and degradation of intact forest ecosystems outside of cities may help control the spread of infectious diseases. Deforestation and land-use changes have been linked to the emergence and spread of pathogens (Karjalainen et al. 2010; Alimi et al. 2021; Austin 2021). For example, forest fragmentation and deforestation in North America is implicated in the increasing incidence of Lyme disease, while climbing rates of deforestation in Asia, Africa, and Latin America have been linked to increases in malaria and malaria vector populations (Karjalainen et al. 2010). Protecting highly biodiverse tropical forests may also prevent spillover of new zoonotic diseases, such as coronaviruses, from animal hosts to humans (Afelt et al. 2018; Sokolow et al. 2019).

Caveats and considerations

Urban trees can also sometimes pose health risks to urban residents, including the following:

• Injury. Branches and tree roots can pose a risk of injury, for example, when roots displace sidewalk paving or when tree limbs (or entire trees) fall on roads or property (Escobedo et al. 2011).
• Zoonotic diseases. Wooded areas may house unwanted animals, such as feral dogs, and pests that carry disease, such as ticks (Lyytimäki et al. 2008; Coutts and Hahn 2015; Lõhmus and Balbus 2015; von Döhren and Haase 2015; Stone et al. 2017).

To reduce these risks, cities may need to pursue targeted interventions. Examples include periodic tree trimming or removing hazardous trees, public education, and population control of animal hosts and vectors (Lyytimäki et al. 2008; Lõhmus and Balbus 2015). City leaders should include funding for tree pruning and removal in city budgets.

Goal 4: Creating Walkable, Safe Streets

Context

Cities around the world are striving to increase opportunities for public transport and active transit (i.e., by foot or by bicycle) as part of their decarbonization strategies. But greener cities are not the only benefit of such efforts. Physical inactivity is a leading global health concern (Kohl et al. 2012), with many harmful effects on the body (Tremblay et al. 2010). Creating more inviting spaces for active transport, physical exercise, and recreation could be a health-environment win-win.

What roles can forests and green spaces play?

Physical activity may explain part of the connection between health and nature exposure (Hartig et al. 2014). But evidence connecting green space directly to increased physical activity remains mixed (Lee and Maheswaran 2011; Nieuwenhuijsen 2018). Evidence suggests green spaces may either have a positive (e.g., Lachowycz and Jones 2011; Calogiuri and Chroni 2014) or neutral (e.g., Hartig et al. 2014; Hankey and Marshall 2017; Kondo et al. 2018) effect on physical activity. In one recent review, however, 18 out of 19 studies suggested a positive effect of urban trees on levels of physical activity (Wolf et al. 2020).

By providing shade, reducing exposure to air pollution, and enhancing aesthetic appeal, street trees might encourage active transport (Figure 6; Kumar et al. 2019; Wolf et al. 2020). Perceived safety, distance to destination, and presence of infrastructure (e.g., sidewalks, bike lanes) also drive decisions related to active transit (Hartig et al. 2014).

Urban green spaces and large, mature trees have been associated with reduced levels of crime, aggressive behavior, and other antisocial activities (Kondo et al. 2015; Wolf and Robbins 2015; Jennings et al. 2016; Wolf et al. 2020). Although evidence remains mixed, researchers have found lower crime rates related to characteristics such as street tree density, when controlling for other confounding variables. For example, increased canopy cover has been associated with reduced rates of homicide in Bogotá (Escobedo et al. 2018), and reduced rates of gunshot assaults in Philadelphia (Kondo et al. 2017). In Baltimore, a 10 percent increase in canopy was associated with a 12 percent decrease in crime (Troy et al. 2012).

Well-placed and well-maintained urban trees also hold the potential to enhance transportation safety. The presence of trees may reduce the number of vehicle collisions (Lyytimäki et al. 2008; Wolf 2010; Van Treese et al. 2017). Trees may also help to demarcate the edge of the road or create a barrier between vehicles and pedestrians (Mullaney et al. 2015).

In addition, urban and nearby forests create spaces for recreation and play (Tyrväinen et al. 2005; O'Brien et al. 2017). Forested areas in and around cities can host hikers, campers, trail runners, birdwatchers, and provide space for children to engage in free play. The cooling and shading provided by trees moderates microclimates, which can encourage use. If accessing areas of urban nature is challenging or expensive, these benefits will not be equitably distributed among populations.

Figure 6 | Trees can be incorporated into urban streets to create favorable microclimates for active transit and play for children

Source: WRI Mexico.

Caveats and considerations

Aspects of urban trees can threaten residents’ safety when commuting or exercising.

• As mentioned above, tree roots can damage sidewalks and some pavements (Randrup et al. 2001; Escobedo et al. 2011; Roy et al. 2012). Careful species and site selection for and maintenance of trees can reduce these risks and ensures accessibility for all users of public infrastructure.
• Poorly placed trees can also be a hazard along roads. Trees and other vegetation may block lines of sight for drivers, bikers, and other commuters (Wolf 2006; Lyytimäki et al. 2008). Species selection, placement, and proper maintenance can reduce this risk.

Urban forests may also affect residents’ perceived safety (Figure 7, top; Kondo et al. 2015; Mancus and Campbell 2018). This is also mediated by the following factors:

• Personal identity. Obstructed views or shaded spaces may increase fear of crime or danger, particularly in women, ethnic minorities, and the elderly—and in those who have experienced crime directly or indirectly in the past (Jansson et al. 2013; Maruthaveeran and Konijnendijk van den Bosch 2014). This depends on the city context.
• Local context and characteristics of the forested area. Poorly maintained, poorly lit, or littered green spaces may be perceived as places for illicit activity or antisocial behavior (Tzoulas et al. 2007; Jansson et al. 2013; Maruthaveeran and Konijnendijk van den Bosch 2014; Kondo et al. 2015; von Döhren and Haase 2015; Wolf 2017).

Figure 7 | Inner Forests and Perceived Safety

Note: Areas with urban trees could make some residents feel unsafe (left), but these spaces can also be intentionally designed or maintained to increase perception of safety and resident comfort for all users (right).

Source: Authors. Adapted from Trivedi et al. 2020.

The quality and accessibility of green spaces affects how people use them for recreation and physical activity (Lee and Maheswaran 2011; Calogiuri and Chroni 2014). As described above, fear of crime may prevent certain groups from being physically active or commuting near these spaces, especially in the dark (Lyytimäki and Sipilä 2009; Jansson et al. 2013). In some contexts, maintaining vegetation and installing infrastructure (lights, etc.) may be necessary to create safe and accessible areas for all residents (Green City Partnerships 2019). Moreover, safeguards may need to be put in place to ensure that green spaces are used in a safe way that allows use by all residents (for example, regulating mountain biking on single-track pedestrian trails).

Goal 5: Supporting Community Connections

Context

Strong social networks in communities form the foundation for thriving cities. Robust social networks may increase community resilience against disturbances such as natural disasters (e.g., Islam and Walkerden 2014; Townshend et al. 2015). In individuals, social relationships and shared trust support health and well-being (Hartig et al. 2014; Braubach et al. 2017) and buffer against stress (Jennings et al. 2016). Such social cohesion can also reduce feelings of loneliness and isolation (Wolf 2017), which have been linked to higher rates of illness and mortality (Kondo et al. 2015; Braubach et al. 2017).

What roles can forests and green spaces play?

Urban forests and other green spaces can enhance social well-being by providing cultural ecosystem services, including benefits such as aesthetic appeal, recreation, and spiritual connection (Millennium Ecosystem Assessment 2005). For centuries, trees have been planted in and around cities to beautify public spaces, gardens, streets, and yards to provide aesthetic benefits as they improve scenic quality or visual appeal (Roy et al. 2012; Säumel et al. 2016) and even produce pleasant smells and sounds (Zhou and Parves Rana 2011).

Furthermore, inner and nearby forests can promote a “sense of place”—the idea of identity and emotional connection to the local environment (Wolf et al. 2014; Jennings et al. 2016; O’Brien et al. 2017). When green spaces increase residents’ connections to their communities, they may be more likely to engage in health-promoting social or physical activities (Jennings et al. 2016). Sense of place may even stimulate economic activity—for example, it can drive the preferences of tourists and their intention to revisit certain locations (Hausmann et al. 2016).

By reinforcing a sense of place and stimulating feelings of attachment and belonging, well-kept green infrastructure may also foster community identity (Jennings and Gaither 2015; Jennings and Bamkole 2019):

• Forests, woodlands, parks, and urban green spaces may also be places for recreating, for gathering culturally relevant foods, or for expressing oneself through photography or art (O’Brien et al. 2017).
• Green spaces, especially those with temperature regulation by trees, can be desirable locations for social interaction (Lee and Maheswaran 2011; Zhou and Parves Rana 2011; Shanahan et al. 2015; Braubach et al. 2017; Nesbitt et al. 2017; Bratman et al. 2019).
• Direct participation in tree-planting programs or other green space stewardship activities may stimulate a sense of community identity and ownership (Higgs 2003; Nowak and Dwyer 2007; Jennings et al. 2016).

Around the world, forests serve as settings for spiritual practice, sacred symbols, and spaces for contemplation for both individuals and groups (Daniel et al. 2012; O’Brien et al. 2017). For some people, forest environments trigger feelings of “awe” or transcendence (Dwyer et al. 1991; Williams and Harvey 2001; Kuo 2015; Irvine and Herrett 2018). Spirituality may mediate the relationship between human well-being and nature (Kamitsis and Francis 2013; Hansen et al. 2017). In addition to specific institutional spaces such as churches, mosques, or other formal structures of worship, forests and green spaces provide space for spiritual practice (Okyerefo and Fiaveh 2017; Ngulani and Shackleton 2019). For example, in Accra, Ghana, the Achimota Forest is considered a sacred place of gathering, where urban dwellers seek serenity (Okyerefo and Fiaveh 2017). In Japan and India, sacred shrine or temple forests have been protected as the areas around them are urbanized—sometimes for centuries (Ishii et al. 2010; Daniel et al. 2012).

Caveats and considerations

As with most benefits, the ways forests can provide cultural benefits should be considered with local context and perspectives in mind:

• The aesthetic preferences of some groups may conflict with others. For example, non-native species are preferred by some, whereas others prefer native natural areas (Lõhmus and Balbus 2015; von Döhren and Haase 2015).
• Spiritual services are not easily generalized or valued in economic terms. Their value may vary widely across urban subpopulations (Daniel et al. 2012).

Goal 6: Reducing Urban Environmental Inequity

Context

The livable and sustainable cities of the future are equitable cities. But technological innovation, urbanization, and migration exacerbate existing income inequality in many nations—and climate change threatens to erase progress in reducing income inequality among nations (UN DESA 2020). Within cities, lower-income and marginalized communities disproportionately inhabit “riskscapes,” which are geographic areas with limited access to resources and high risk of exposure to environmental stressors and hazards such as pollution and natural disasters (Jennings et al. 2012; Kondo et al. 2015).

Inequality in the distribution, funding, and maintenance of urban tree canopies is an environmental justice issue (Jennings and Gaither 2015; Schwarz et al. 2015). Lower levels of urban tree canopy cover have been associated with lower-income populations (Schwarz et al. 2015; Jennings et al. 2016; Gerrish and Watkins 2018) and with racial or ethnic minority populations (Watkins and Gerrish 2018; Locke et al. 2021) in some cities (Jennings et al. 2016). Developments in monitoring technology are making it easier to identify and correct these trends. In 2021, for example, American Forests released its Tree Equity Score tool—which reflects levels of tree canopy cover and demographic income such as race or age in around 150,000 neighborhoods in 486 municipalities in the United States—providing valuable data to residents and community leaders alike.¹⁷

What roles can forests and green spaces play?

Forests in and around cities, as well as other types of green infrastructure, may be managed, protected, or expanded in ways that can help reduce inequities between groups of people. Addressing inequities in tree distribution helps to distribute the important health benefits provided by forests across all residents. Evidence suggests that lower-income and marginalized groups may benefit from the expansions in urban canopy cover (or other urban greening efforts) more than other groups (Braubach et al. 2017). For instance, access to and engagement with urban green spaces by lower-income and marginalized groups may reduce disparities in rates of cardiovascular disease, obesity, heat stress, or psychological illness (Jennings and Gaither 2015). Urban forest planting, management, and stewardship also present opportunities for employment as well.

Caveats and considerations

Careful planning is required to ensure that inner forest expansion does not exacerbate existing disparities in health and well-being in cities (Kondo et al. 2015; Jennings et al. 2016). Expanding urban forests (or other green infrastructure) may inflate property and housing costs in a way that burdens or contributes to the displacement of low-income residents in these areas—a phenomenon coined as eco-gentrification (Wolch et al. 2014; Wolf 2017). A scoping review of 15 empirical studies found that longtime residents who are negatively impacted by green gentrification can experience a lower sense of community and belonging, which may result in lower green space use when compared with newcomers (Jelks et al. 2021). Additionally, residents inhabiting rental properties may either lack the authority or incentive to plant trees on the property (Heynen et al. 2006).

To avoid unintended negative outcomes for residents and to provide benefits to those most in need, city leaders should work with community leaders and local grassroots organizations at every stage of forest planning, management, and development. When communities are not adequately engaged and consulted, well-meaning initiatives may fail to meet their objectives; for example, in Detroit nearly 24 percent of residents approached by a nonprofit declined to have trees planted in their yards, citing insufficient engagement and concerns about a lack of tree maintenance by the city in the past (Carmichael and McDonough 2018). Although inclusive governance and authentic community engagement can require greater investment of time and resources, it can help to prevent unintended negative outcomes and ensure that residents’ needs are met. This will ensure that trees and other green infrastructure are installed where they are most needed and in ways that reflect community preferences.

Goal 7: Ensuring Provision of Food, Medicine, and Raw Materials

Context

As urban populations climb, cities grapple with issues of food security and nutrition (Crush and Frayne 2011). Many city residents lack access to fresh, nutritious food, leading to inequities in health among residents (Dixon et al. 2007). Still others lack adequate access to health care, cooking fuel, or raw materials for trades or crafts.

What roles can forests and green spaces play?

Forests—including those within cities—play an important role in supplying cultivated and foraged foods and medicines as well as other raw materials. Although cities rely heavily on imported goods and materials, opportunities to meet residents’ needs using urban and peri-urban ecosystems may help to address disparities in access among low-income or marginalized groups while reducing pressure on natural rural ecosystems near cities. Examples include the following:

• In urban areas, forests can provide foods, fuel, and medicine, particularly to low-income or marginalized groups, particularly in developing countries (Karjalainen et al. 2010; Pramova et al. 2012; Lwasa et al. 2015; Wolf and Robbins 2015; Lindley et al. 2018). Such products may serve as invaluable safety nets—especially for low-income communities most at risk (Pramova et al. 2012).
• Trees on the urban fringe provide fuelwood, medicine, food, and even products that can be sold for income, particularly in developing countries. This is especially the case for low-income residents and those who live in informal settlements (Shackleton et al. 2015). For example, wood gathered from urban and peri-urban eucalyptus plantations makes up the livelihoods of marginalized groups—primarily women—in Addis Ababa, Ethiopia (Fetene and Worku 2013). Urban foraging for foods and medicines can connect individuals to their cultural heritage or increase food security (Poe et al. 2013).
• Trees—especially nitrogen-fixing species—may also complement agriculture in and around cities (Pramova et al. 2012). Integrating trees into farmland to improve or diversify agriculture (agroforestry) can ameliorate microclimate for crops, improve soil fertility, and reduce water stress, depending on the crop type and region (Pramova et al. 2012).
• Trees in and around cities can diversify incomes by supplementing crop production, supporting animal husbandry, or providing raw materials (Salbitano et al. 2016). In the Pacific Islands, agroforestry in home gardens has historically enhanced diet diversity and provided raw materials for construction and craft making (Thaman et al. 2006).
• Forest plants, fungi, and microbes represent an enormous reserve of compounds with potential pharmaceutical or nutritional value (Karjalainen et al. 2010). Even the urban forest can provide medicines that may be of particular importance to certain ethnic or cultural groups or to marginalized individuals. The medicinal value of the urban forest has been recognized in North America (Poe et al. 2013), Latin America and the Caribbean (Dobbs et al. 2019), and other regions.
• By providing wood for fuel or timber, urban forests may also help shield some natural forests from overexploitation (Salbitano et al. 2017).

Caveats and considerations

To maximize these benefits, urban decision-makers should consider the following:

• Some municipal policies and regulations specifically prohibit foraging and gathering from urban trees or woodlands (Shackleton et al. 2017).
• Urban foraging and gathering may shield intact rural forests from overexploitation, but plants and fungi of the urban forest are also vulnerable to overharvesting (Shackleton et al. 2017). Investing in management and harvesting strategies is essential to prevent overuse.
• When urban food cultivation takes place near road corridors or rights-of-way, it may be necessary to create barriers between the roadside and urban agriculture to reduce the risk of pollutant uptake by crops (Säumel et al. 2016).

Goal 8: Enhancing Economic Well-Being

Context

Healthy cities are also economically secure cities. To be resilient, communities need to provide economic opportunities to residents and bolster small businesses. They also need to harness the power of nature to reduce municipal costs and address multiple problems simultaneously.

What roles can forests and green spaces play?

In some contexts, installing or managing urban trees can pay for itself through benefits accrued by the municipality and property owners (Nowak and Dwyer 2007). Estimates of benefit-cost ratios of urban trees vary widely, depending on species and location, from around 5:1 to 24:1 in a global review of studies (Roy et al. 2012). And because larger, more mature trees can provide more benefits, such as shade or air filtration, healthy and properly maintained urban forests represent a municipal capital investment that may actually appreciate in value over time (Stagoll et al. 2012; Salbitano et al. 2016).

Urban forests provide multiple economic benefits to municipalities and their residents:

• Iconic forests and urban vegetation can stimulate tourism (Nesbitt et al. 2017; Salbitano et al. 2017) and green infrastructure in general (Wolf and Robbins 2015; Nesbitt et al. 2017; O’Brien et al. 2017). Research from North America also suggests that consumers may prefer shopping districts with greater numbers of trees, a preference reflected in the duration of time and their willingness to pay for various products (Wolf et al. 2005).
• The presence of trees can increase property values (Nowak and Dwyer 2007; Roy et al. 2012; Mullaney et al. 2015; Nesbitt et al. 2017) in residential, rental, and commercial contexts. Adjacency or proximity to woodlands, urban parks, and other green infrastructure may also increase property values (Wolf and Robbins 2015; Jennings et al. 2017; Nesbitt et al. 2017; O’Brien et al. 2017). But green spaces and urban trees do not influence property values in all global contexts, due in part to perceived issues of safety or security (Cilliers et al. 2013).
• The presence of trees can increase municipal revenue related to increased property taxes (Nowak and Dwyer 2007) or fees associated with tree removal during development.
• Managing urban forests and green infrastructure can provide “green jobs” in nurseries, tree-care services, forest management, and other related areas (Case Study 2; Kondo et al. 2015).
• In some cases, urban tree maintenance costs can be recouped when urban wood waste is repurposed. In the United States alone, waste from urban trees, yard waste, and even demolition could be worth an estimated $89—$786 million when repurposed into wood chips, lumber, and fertilizer (Nowak et al. 2019).
• Forests can reduce energy costs in both residential and commercial settings and can reduce costs related to water management (see Sections 3 and 4 for more details).
• As described above, the presence of trees and other green infrastructure could reduce public health costs, including those related to exposure to extreme heat and air pollution or improved mental health status. For example, findings from a recent analysis of the heat-related benefits of existing urban forests in the United States suggest that urban trees can provide between $17 and $42 per capita (for the entire United States) per year in benefits related to avoided death, illness, and electricity use alone, compared to the typical $5 per capita in expenditures necessary for urban forest maintenance (McDonald et al. 2020).

Caveats and considerations

Although they provide numerous benefits to economic well-being, urban trees are often costly. Like other urban assets and infrastructure, urban forest maintenance and management requires capital related to pruning, planting, emergency tree removal, and damage to pipes or roads by roots. Potential disservices may include damage to infrastructure, such as sidewalks (Randrup et al. 2001) or private property (Escobedo et al. 2011; Cilliers et al. 2013). Recognizing these costs creates realistic expectations for municipalities and encourages proactive, informed planning and management.

It is also important to consider the distribution of these benefits. By increasing land value and rental prices, proactive management or expansion of the urban forest may generate direct revenue for local governments—a win for tight-strapped municipalities. At the same time, increases in property value and subsequent increases in property taxes may place a financial burden on some property owners (Nowak and Dwyer 2007) or even contribute to their displacement (Wolch et al. 2014). To ensure that urban forest expansion and urban greening do not burden low-income residents, these projects should be tailored to suit local contexts and should incorporate extensive community input.

Concluding Thoughts

Forests and nature are important to human health and well-being in cities. Well-planned, well-protected, and well-managed forests in and around cities can ensure that residents have access to a suite of ecosystem services, including ameliorated microclimate and air quality, recreation, mental restoration, and much more. Forests and other green infrastructure can help to reduce poverty, increase social cohesion, and bring communities together, but these outcomes are more likely when community perspectives and needs are incorporated at all stages of forest planning and management.

Integrating trees and forests into city plans to support health and well-being is not always easy. For example, although the value of urban forests for recreation, heritage, and aesthetic value has been recognized in low- and middle-income nations, such as in Latin America and Africa, local governments often do not act to implement forest-based solutions—in part because of the need to prioritize pressing issues, such as access to housing and sanitation (Cilliers et al. 2013; Dobbs et al. 2019). And it may take years or even decades to reap some of the benefits created by trees and other green infrastructure. Yet few interventions offer as many potential cobenefits as urban forests.

For urban health and well-being, forests can offer diverse and dispersed benefits that cities need now more than ever. Many city residents have limited access to interact with forests and nature, and in many places these environments are increasing in use and declining in quality (Bratman et al. 2019). Urban leaders envisioning the vibrant, habitable cities of the future should integrate forests as NBS and essential aspects of urban infrastructure.

Background

Cities around the world face multiple challenges in providing residents with adequate, clean water (Juno and Pool 2020). Extensive urbanization and population growth, land conversion, and water diversion have put pressure on local and regional water supplies in and around cities. Ongoing climate change threatens to disrupt water cycles even further, increasing the incidences of both drought and flooding. Water-related challenges have an impact on the economy, human health, and overall city resident well-being. These are the main water-related challenges for cities:

• Too dirty. Many cities are unable to provide their residents with an essential and basic service: a reliable supply of clean drinking water. Contaminated or unclean drinking water causes severe health issues in many regions. Water treatment facilities and infrastructure are costly to establish and maintain.
• Too much. Flooding threatens the lives and safety of 15 million people as a result of coastal flooding and 132 million people as a result of riverine flooding, putting at risk $177 billion and $535 billion in urban property, respectively (Ward et al. 2020). Safeguarding water and preventing flooding are essential services to urban residents and a key agenda item for many city leaders.
• Too little. Water scarcity can be caused by extreme drought, depletion of groundwater, or reduced river flows. Many cities around the world—especially in arid regions—face seasonal or year-round issues with water supply, which are likely to increase as populations grow.
• Too erratic. City residents—like much of the world—are also vulnerable to the increasingly erratic weather patterns, including longer and more intense droughts and heavy rainfall (Seneviratne et al. 2012). Variability and unpredictability in precipitation and water supply create additional challenges for urban leaders. Shifting precipitation patterns at the global scale—driven by climate change and land-use change—may exacerbate existing issues related to flooding or water scarcity.

To face these water challenges, leaders—from China to the United States to Brazil—are embracing NBS such as forests to complement traditional “gray” city water infrastructure solutions. Increasing areas of forest and green space in strategic locations in cities can reduce burdens on aging or overburdened water infrastructure while delivering key cobenefits. And in contrast to gray infrastructure, green infrastructure can appreciate in value over time.

Scientific evidence suggests that forests and trees can help address all four of these challenges. In this section, we outline the forest benefits:

• Provide cleaner water. Forests help to filter sediments and pollutants from the water upon which cities rely. Forested watersheds, in particular, provide higher-quality water than other land uses because forests filter pollutants and prevent erosion and sedimentation of streams and rivers (Brauman et al. 2007; Calder 2007).
• Help reduce flooding. Within cities, forests intercept rainwater and reduce the burden of stormwater on built water infrastructure, reducing the risk of combined sewer overflows and flooding (Figure 8). Trees and other vegetation in bioretention areas, green roofs, and bioswales can complement traditional “gray” water infrastructure (i.e., engineered systems using materials such as concrete and steel) solutions for stormwater management in urban areas (Berland et al. 2017). Forested watersheds regulate flows and help prevent flooding and landslides.
• Protect water supply. Forests in and around cities can replenish groundwater supplies and help sustain rainfall patterns and regulate quantity across seasons (Neary et al. 2009; Ellison et al. 2017).
• Support healthy hydrological cycles. Forests play a vital role in global regulation of water cycling, which supports sufficient precipitation in cities and in agricultural regions key to supplying cities with food. Forests (especially large, intact rain forests) can affect hydrological cycles and rainfall patterns hundreds to thousands of miles away by “recharging” atmospheric moisture supplies (Ellison et al. 2017). This linkage between faraway forests and climate hundreds or thousands of miles away has substantial implications for urban residents and global food security (see Box 1 in Section 4). And because of the key role forests play in the global carbon cycle, climate change mitigation by forests may also help to prevent further shifts towards extremes.

Why context matters

Forest benefits related to water will vary with the local context. The effects of watershed deforestation on water quantity, including seasonal flow regulation, depend on the local geographical context, climate, and the type of forest. The impacts of reforestation on water also depend on the context, such as species used and other elements of planting design. Reforestation may even negatively affect water availability in the near term (Filoso et al. 2019). Additionally, the effects of climate change may alter forest-water interactions (Jones et al. 2020).

Figure 8 | The Role of Trees and Forests in the Water Cycle

Notes: Simplified hydrological cycle, showing (1) the role of forests and other vegetation in intercepting and recycling precipitation, which is then transported across landscapes, and (2) the role that forests play in promoting infiltration and deep infiltration into groundwater sources.

Source: Authors. Adapted from Ellison et al. (2017) and Bonnesoeur et al. (2019).

Water Challenge 1: Too Dirty

Context

Most cities draw water from local watersheds. Development, industrialization, land-use change, and deforestation in catchment areas above cities can lead to problems related to sedimentation, eutrophication, and contamination by pollutants—including sewage, microplastics, hormones, and other pharmaceutical products and chemicals from mining processes—which all translate to reductions in water quality (McGriff 1972). Combined, these issues may increase burdens on water filtration and treatment facilities, passing on a slew of added considerations and unexpected costs to cities and water utilities.

What roles can forests play?

The protection of water quality—a measure of the pollutants, nutrients, microbes, and sediment present—is an important benefit of both inner and nearby forests (Brauman et al. 2007). Watersheds covered by forests tend to have superior water quality and less sedimentation than degraded watersheds and can also reduce water treatment costs. In fact, 33 of the world’s 105 largest cities currently rely on forested protected areas to supply their water (Dudley and Stolton 2003). City source watershed degradation is widespread globally, with 9 in 10 watersheds having lost significant amounts of natural land to agriculture and urbanization, resulting in increased water treatment costs for 1 in 3 large cities globally (McDonald et al. 2016). This close interconnection means that clearing and degrading forests in watersheds can affect municipal water supply.

Forests support water quality in urban areas and watersheds by the following actions:

• Increasing infiltration and reducing rates of erosion, thereby preventing sedimentation of streams and rivers (Neary et al. 2009; Carvalho-Santos et al. 2014; Tellman et al. 2018), reducing treatment costs
• Absorbing or transforming contaminants from both soil and water (e.g., heavy metals, hydrocarbons, pesticides; Brauman et al. 2007; Luqman et al. 2013)
• Tightly cycling nutrients (Neary et al. 2009), reducing the likelihood of eutrophication (i.e., excessive concentrations of nutrients in a body of water) that can contribute to algal blooms and “dead zones” in water bodies
• Stabilizing riverbanks and steep slopes (Brauman et al. 2007), which also reduces soil erosion and sedimentation of waterways
• Shading streams and rivers, which maintains conditions for aquatic biodiversity (Richardson and Béraud 2014)

Forest loss, however, can impair water quality. Compared with forests, industrial or agricultural land uses generate pollution and reduce the landscape’s capacity to intercept pollution and sediment (Postel and Thompson 2005). Grazing, logging, and the construction of roads may all further degrade forest ecosystems and can dramatically increase runoff (Brauman et al. 2007; Bonnesour et al. 2019).

Inner forests

Trees can be incorporated into various “green infrastructure” or hybrid “green-gray” systems designed to capture and filter stormwater. In doing so, they can reduce sedimentation and pollution carried in surface runoff (Browder et al. 2019). For example, in Portland, Oregon, urban green infrastructure reduced flooding in the city by up to 94 percent and filtered 90 percent of pollutants, leading to $224 million in water infrastructure savings (City Parks Alliance n.d.). Trees also played an important role in Philadelphia’s Green City, Clean Waters initiative (Case Study 2).

Targeted tree plantings may offer benefits in highly contaminated urban areas. In a process called phytoremediation, targeted plantings on contaminated urban lands may offer a low-cost method to reduce soil and water contamination while providing other cobenefits, such as increased aesthetic appeal (Song et al. 2019).

Nearby forests

Water from forested watersheds is typically higher quality than water from watersheds with other land uses, such as agriculture or industry (Brauman et al. 2007; Calder 2007). Protection of forested watersheds can lower the costs of a clean water supply for cities downstream:

• Forests can act as buffers for bodies of water. The protection or planting of trees between agricultural fields and streams or rivers can reduce surface runoff of contaminants and nutrients into these water supplies (Brauman et al. 2007; Luqman et al. 2013). To provide and conserve habitat for biodiversity and maintain temperatures, riparian buffers of at least 30 m or more are recommended (Sweeney and Newbold 2014).
• Ecologically sensitive forest management can reduce unwanted inputs into waterways. In forest plantations on former agricultural lands, the adoption of management practices to conserve soil and reduce erosion can reduce sedimentation and nutrient loading into local rivers and streams (van Dijk and Keenan 2007). In Colorado, following two catastrophic wildfires in 1996 and 2002, it was estimated that the inflow of debris and sediment into Denver Water’s main reservoir resulted in $26 million of city expenses to repair damaged water infrastructure and even more investment to restore its source watersheds in an effort to reduce future water treatment costs (Gartner et al. 2013).
• Upstream forest protection and restoration can reduce costs for water utilities. A cross-city analysis found that upstream forest protection and restoration can reduce costs for water utilities in the world’s 534 largest cities by $890 million per year collectively (McDonald and Shemie 2014). Analysis from Rio de Janeiro suggests that restoring nearby forests could save the city up to $79 million in water treatment costs alone over 30 years (Feltran-Barbieri et al. 2018) and that restoring 4,000 ha of forest in São Paulo’s Cantareira watershed could reduce sediment pollution by 36 percent in 30 years and reduce water turbidity by almost half, resulting in a 28 percent return on investment for the region’s water utility, Sabesp (Ozment et al. 2018). And yet, globally, these cost-saving nearby forests are being rapidly lost. In the world’s major city watersheds, tree cover has fallen from a historical average of 68 percent to 29 percent, according to data from Global Forest Watch Water (Springgay et al. 2019).

Caveats and considerations

Water quality benefits differ with context, and each individual effort to improve water quality that uses forests needs to consider site-based conditions and be designed based on observed, empirical data:

• Trees can contribute organic matter such as leaves and branches to waterways, which may contribute to excessive nutrient levels in local waterways, possibly decreasing the safety of drinking water (Pataki et al. 2011; Decina et al. 2020).
• In arid and semiarid regions where ecosystems have been degraded, reforestation of watersheds can slow or reverse salinization, increasing the quality of water resources and potentially making nonpotable water potable (Brauman et al. 2007).
• Sedimentation of surface waters may increase in poorly managed plantation forests, where erosion is significant due to the lack of forest understory and the presence of roads and heavy machinery (Calder 2007).
• Benefits can change over time and differ with the age of the forest; for example, younger forests do not provide the same water quality benefits as older, more mature ones (van Dijk and Keenan 2007).
• Seasonal considerations affect benefits, where the water purification services from trees that go dormant during the dry or winter seasons are not as high as those from evergreen forests or where there is no seasonal change (van Dijk and Keenan 2007).

Water Challenge 2: Too Much

Context

In and around urban areas, flooding—including pluvial, fluvial, and coastal—presents enormous risks to economic security and human safety. Poorly planned urbanization can compound these risks (Jha et al. 2012). Inhabitants of informal settlements are particularly vulnerable to the effects of flooding, both directly and in terms of structural damage (Jha et al. 2012; De Risi et al. 2013). Flooding can also lead to death, injury, water- and animal-borne diseases, and psychological trauma (Ahern et al. 2005). From 1995 to 2015, floods affected more than 2.3 billion people, mostly in Asia (CRED 2015).

The dangers posed by flooding continue to grow. The number of people impacted by river flooding over the next decade is expected to double to 132 million people annually (Ward et al. 2020). It is estimated that flood losses may total $1 trillion annually by 2050 under business-as-usual scenarios and approach $60 billion annually by 2050, even with significant adaptation measures. The most devastating impacts are projected to be in low-lying cities such as Guangzhou, China; and New Orleans (Hallegatte et al. 2013).

The urban environment is prone to problems with flooding:

• Urban areas contain high amounts of impervious (sealed) surfaces, which means rain events create runoff more quickly and peak runoff (flood) levels are higher (Figure 9; Douglas 2008). These sealed surfaces also decrease groundwater recharge, which in turn reduces regular flow of water in streams (McGriff 1972). Even soils and lawns in urban areas can become so compact that they act as impervious surfaces (Douglas 2008). These sealed surfaces also increase the likelihood of flooding: a 1 percent increase in impervious surfaces can increase the annual flood magnitude by 3.3 percent (Blum et al. 2020). Surface or street ponding and overflow (pluvial flooding) driven by rainfall may contribute to combined sewage overflows or residential flooding (Rosenzweig et al. 2018).
• Urban areas tend to rely on extensive built infrastructure with a finite capacity. Old or deteriorated infrastructure may be insufficient to manage the increasing variability in precipitation associated with climate change.
• Urbanization transforms the characteristics of rivers and streams as floodplains in urban areas are typically cleared of vegetation and streams may be channelized, redirected, or buried (Douglas 2008). These highly modified streams surrounded by impervious surfaces often flood quickly.

Figure 9 | Water Infiltration in Natural Areas versus Urban Areas

Source: Authors. Adapted from PWD (n.d.).

What roles can forests play?

Inner forests

The urban forest can reduce stormwater runoff and associated flooding (Figure 10) by

• intercepting and delaying water during rain events, reducing the amount of stormwater runoff (Berland et al. 2017; Kuehler et al. 2017), potentially reestablishing a hydrological cycle more closely resembling local historical conditions;
• altering soil water-holding capacities to promote infiltration (entry) and percolation (downward movement) of rainwater in the soil (Berland et al. 2017; Kuehler et al. 2017; Zhang and Chui 2019); and
• increasing the amount of water returned to the atmosphere by evapotranspiration (Berland et al. 2017; Kuehler et al. 2017; Jones et al. 2020). In doing so, trees free up space in soil, making room for stormwater storage in the future (Berland et al. 2017; Kuehler et al. 2017; Berland et al. 2017). Evapotranspiration also has a cooling effect and helps to mitigate the urban heat island effect (Berland et al. 2017).

As a result, cities with healthy urban forests often enjoy a number of benefits, including the following:

• Reduced burden on sewer systems. In combined stormwater and sewage systems, heavy rainfall can lead to a combined sewage overflow of thousands or millions of gallons of untreated sewage into nearby lakes and streams, potentially compromising the safety of drinking water supplies and the quality of aquatic habitats. By reducing the total amount of surface runoff during a storm event, the urban forest can help to reduce the likelihood of combined sewage overflows (Berland et al. 2017).
• Reduced stormwater volume on surfaces. By increasing infiltration, trees and other elements of green infrastructure provide space for rainwater storage, reduce surface runoff and pollutant inputs to local waters, and promote groundwater recharge and increased baseflow (Case Study 3; Zhang and Chui 2019).

Figure 10 | Urban Trees and Rainfall

Source: Authors. Adapted from Marritz (2013).

Nearby forests

Outside city boundaries, natural forests can offer protection from small- and medium-sized floods, moderating the severity of impacts on both people and property (Lele 2009; Carvalho-Santos et al. 2014). This is true particularly along rivers and coasts (Lele 2009; Bhattacharjee and Behera 2018). Protection and restoration of forests in upstream areas can help to reduce peak streamflow and thus reduce the risk of river flooding. Trees lower flood risk by increasing infiltration in the soil, storing excess runoff, and slowing the release of water (Gunnell et al. 2019). In this sense, healthy forest ecosystems often act as “sponges” (Laurance 2007). Conversely, some research has linked forest loss to increased flooding frequency (Bradshaw et al. 2007), but more research is needed to better substantiate the link. Forested riparian zones (the areas immediately adjacent to rivers) and floodplain forests can also help to stabilize banks and restore natural river flow, further reducing the chance of flooding (González et al. 2017). Mangroves play an especially important role near coastal cities (Case Study 4).

Caveats and considerations

Urban leaders seeking to maximize the stormwater benefits of their urban forests should consider the following:

• Built environment modifications. To address urban flooding, it may also be necessary to increase the area of permeable surfaces and to promote connectivity between stormwater retention areas (Phillips et al. 2019).
• Synergies with other NBS. Strategically incorporating trees into other green infrastructure can make these interventions more effective. For example, trees planted in bioswales, green roofs, and bioretention basins may help to address pluvial flooding and restore predevelopment hydrological function (McDonald and Shemie 2014).
• Limitations on capacity. Although green infrastructure and urban forests can relieve some of the pressure on traditional infrastructure, cities will still need to consider multiple options to handle excess water—especially related to coastal and river flooding from climate change.

Flood prevention benefits of nearby forests are limited. Although existing forests can attenuate some flood-related risks, forest restoration is unlikely to have a significant impact on large-scale floods or extreme weather events, which can quickly overwhelm a forest’s absorption capacity (Calder 2007; Ellison et al. 2017).

In some contexts, afforestation (planting trees where forests historically did not occur) with plantation forests can also reduce peak flows and the risk of flash floods following medium- to large-scale rain events in small catchments (van Dijk and Keenan 2007). However, the effect of plantation forests on large landslides is probably negligible and is currently poorly understood (van Dijk and Keenan 2007). Overall, the outcomes of afforestation on water may be unpredictable, and other interventions are generally better suited to address larger floods, including discouraging human settlement in floodplains (FAO and CIFOR 2005; van Dijk and Keenan 2007).

Water Challenge 3: Too Little

Context

About 25 percent of the world’s population faces extreme water stress (Hofste et al. 2019). Climate change and a growing population are projected to ramp up pressure on finite water supplies. Flörke et al. (2018) find that one in six large cities will face water deficits in the future. With more than 50 percent of the world’s population concentrated in cities, urban water scarcity can have dire economic and health impacts. For example, the “Day Zero” drought-induced water crisis in Cape Town of 2017–18 resulted in the loss of thousands of jobs, dramatically reduced regional agricultural production, and put many more people at risk for diseases due to inadequate sanitation (Parks et al. 2019).

What roles can forests play?

Forests around cities play a vital role in protecting and sustaining water supplies (Figure 11). Maintaining forests in watersheds is generally positive for regulating water supply across the year. Deforestation and forest degradation in watersheds jeopardize water availability by altering local hydrology and reducing interseasonal stability in water supplies.

Nearby forests

Forests drive downwind and interior precipitation. Forested areas often “use” more water than other ecosystems on a local scale because they have high evapotranspiration rates (Brauman et al. 2007). But from recent theoretical research, scientists have begun to posit that this water, rather than being “lost,” serves as an important source for precipitation in downwind regions (Ellison et al. 2012; Ellison 2018). By capturing and recycling precipitation, evapotranspiration sends water into the atmosphere, where it can fall as rain in downwind regions (Ellison et al. 2017). For example, coastal forests can capture and transpire fog and humidity from oceanic winds, carrying it deeper into continental interiors than it might otherwise travel (Ellison et al. 2017). Thus, even forests beyond watershed boundaries can influence water availability and provide key water regulation services to agricultural and urban areas (Melo et al. 2021).

Figure 11 | How Forested Watersheds Protect Water Supplies

Source: Authors. Adapted from Qin and Gartner 2016.

Intact forests in watersheds can reduce seasonal fluctuations in water availability. Forests generally use more water than other land uses (with the exception of irrigated crops), which means that forestation can reduce flows in catchments, and forested watersheds may have similar or slightly lower streamflow than nonforested catchments (Calder 2007; Carvalho-Santos et al. 2014). But forests play a key role in water regulation throughout the year: they reduce the impact of floods in wet periods and help to mitigate the impacts of droughts in dry periods (Neary et al. 2009). Consequently, forest conversion and degradation may lead to increased water flows in the wet season but reduced dry season flows in many contexts (Lele 2009). Forests increase the infiltration capacity of the soil, which promotes groundwater recharge (and reduces flood peaks), helping to stabilize flows throughout the year and benefiting areas far downstream. Soil penetration by tree roots improves the capacity of soil to store water, as does the presence of organic material from decaying plants and chemicals released by plants and other forest organisms in the soil (Brauman et al. 2007; Neary et al. 2009).

Montane cloud forests, for example, can be vital sources for water contribution during the dry season. Foliage in cloud forests in mountainous regions captures the water vapor of clouds, which run down the stems and leaves of plants and thereafter into soils and streams. Cloud forests have especially pronounced effects in drier regions (Postel and Thompson 2005). Fog capture can provide as much water as rain in many of these regions, which can be especially important for maintaining stream flow in the dry season (Ellison et al. 2017).

Avoiding deforestation is key for regulating water quantity in ecosystems. Deforestation can increase local water availability (Brauman et al. 2007; van Dijk and Keenan 2007; Ellison et al. 2012; Ellison et al. 2017; Filoso et al. 2017; Zhang et al. 2017), which, in water-scarce regions, may seem like a benefit. But deforestation often also increases runoff and short-term streamflow and can thus increase soil degradation and flood frequency (Brauman et al. 2007). The increase in surface water is only part of the picture: deforestation often decreases infiltration rates, leading to higher peak flows but reduced groundwater recharge and reduced dry season flows—two factors extremely relevant to land-reliant livelihoods in the tropics (Ellison et al. 2017). Short-term gains in water availability following deforestation do not make up for other important lost services, such as the regulation of water availability throughout the year between seasons, prevention of sedimentation, and reduced water treatment costs. For example, in Malawi, analysis of satellite data and household surveys showed that a 1 percent increase in local deforestation decreased household access to clean drinking water by 0.93 percent, suggesting that the deforestation Malawi has experienced in the last decade may have effectively had the same impact on water access as a 9 percent reduction in rainfall in the region (Mapulanga and Naito 2019).

Caveats and considerations

In contrast with the benefits of forests conservation or avoided deforestation, however, reforestation or restoration of degraded forests may reduce year-round water availability, at least in the short run, and particularly in arid or semiarid regions (Filoso et al. 2017). This is because forests generally increase water infiltration into soils and evapotranspiration, reducing the availability of water for other uses (Ilstedt et al. 2007; Filoso et al. 2017; Lozano-Baez et al. 2019). Trees planted in former shrublands or grasslands may reduce both flood peaks and low flows (Brauman et al. 2007). In some cases, infiltration rates can exceed evapotranspiration rates, with net positive effects on groundwater recharge. But in general, evidence suggests planting new forests typically has negative or neutral effects on annual catchment (surface water) flows (Calder 2007).

Furthermore, not all forest types provide equal benefits. Compared to native forests, plantation forests reduce water runoff, with negative effects on water supply (Case Study 5; Lele 2009; Alvarez-Garreton et al. 2019; Yu et al. 2019). Unlike native forests, plantations can put pressure on surface water quality and supply.¹⁸ In particular, planting native grasslands or other native ecosystems with non-native trees, or planting non-native trees that use water inefficiently, can reduce dry season water availability (Postel and Thompson 2005). Fast-growing plantation species can reduce flows in catchments, especially while the trees are young (Brauman et al. 2007; Calder 2007; van Dijk and Keenan 2007; Bonnesoeur et al. 2019; Jones et al. 2020). For example, plantations of water-intensive eucalyptus have been shown to dramatically reduce surface runoff and streamflow in multiple climates, with effects persisting for decades (Case Study 5; Farley et al. 2005). Although these reductions may be desirable in certain watersheds (e.g., those struggling with salinization issues or highly degraded former agricultural lands), they could further endanger water supplies in many areas (Farley et al. 2005; Brauman et al. 2007; van Dijk and Keenan 2007).

Water Challenge 4: Too Erratic

Context

Erratic and unpredictable weather—including extreme drought, torrential rainfall, and violent storms—continues to make global headlines and affects millions of people annually. Although some variability and extremes of climate are natural, evidence suggests that anthropogenic climate change has increased the frequency, intensity, and duration of many of these events (Seneviratne et al. 2012). Precipitation and drought are both expected to increase during the 21st century (Seneviratne et al. 2012). In addition to the effects of changing atmospheric GHG levels, large-scale changes in land cover affect climate locally, regionally, and globally by altering surface temperature, humidity, evaporation, cloud formation, precipitation, and more (Mahmood et al. 2014).

Cities are vulnerable to these types of changes. Increases in flooding, drought, or heavy rainfall within the immediate vicinity of cities presents obvious challenges to urban leaders. Additionally, as net importers of water, food, and materials, cities rely on the functioning of productive ecosystems outside their boundaries. The vast majority of urban demand is met by goods imported from far beyond city boundaries—from rice to milk to timber. This means that cities both rely on food produced in the world’s major agricultural areas and have significant effects on the world’s forests via city consumption patterns. Thus, disturbances in supply chains due to increasingly erratic weather patterns around the world may have indirect impacts on cities too.

What roles do forests play in global precipitation patterns?

The world’s large and intact forests play an important role in cycling and transporting water, thereby shaping global and regional weather patterns. Forests—especially intact tropical forests—affect large-scale weather patterns. Forests regulate regional and global precipitation patterns, which impact both city water supply and the production of food to city residents in key agricultural regions (Lawrence and Vandecar 2015). Because land cover change is associated with changes in precipitation and climate (Mahmood et al. 2014), the persistence of forests can be a stabilizing factor.

Evapotranspiration by forests cycles large amounts of precipitation into the atmosphere, creating “flying rivers” (atmospheric currents laden with moisture capable of driving weather patterns in distant locales). Forests effectively recycle rain by returning moisture to the atmosphere, which contributes to future rain events (Ellison et al. 2012). This recycled “green water” released during evapotranspiration affects local areas, as described in the previous section, and also composes a large portion of the world’s rainfall in locations far away. The emerging scientific literature on tropical forests and their impact on global air circulation, also known as teleconnections, highlights how these processes change when tropical forests are cleared, and how this affects global precipitation patterns.

Forests move water from the earth’s surface to the atmosphere at large scales. Tropical forests contain air that is warmer and more humid than in surrounding areas, creating a low-pressure zone that drives wind patterns (Makarieva and Gorshkov 2010). It is estimated that the moisture moving over the Amazon rain forest is recycled five to six times as it moves westward across the continent (Lovejoy and Nobre 2018). Deforestation drastically reduces evapotranspiration rates and, with them, the movement of water.

Current forest practices and risks for the hydrological cycle

Three major tropical forests disproportionately affect global water cycles:

• Amazon rain forest. The largest tropical forest in the world exerts great influence over regional (Davidson et al. 2012) and global precipitation and air circulation (Lawrence and Vandecar 2015).
• Congo Basin (Figure 12). This forest region in Central Africa drives precipitation patterns around Africa (Gebrehiwot 2019) and beyond (Lawrence and Vandecar 2015).
• Southeast Asian rain forest. The smallest of all three tropical forest basins—but the most humid and with the highest rainfall—the Southeast Asian rain forest influences the climate within and beyond the region through impacts to the Asian monsoon circulation, potentially resulting in higher rainfall in some areas and lower rainfall in others (Lawrence and Vandecar 2015).

Figure 12 | Forest Cover, Water Risk, and Water Movement

Notes: Because forests require more water than ecosystems such as grasslands, it is no surprise that forest cover (Box A) often coincides with areas of lower water risk (Box B). But as Box C shows, water also moves throughout the atmosphere, directed by winds. The loss of forests in Central Africa could have cascading impacts on those who depend upon the Nile River, for example, which is fed by precipitation from both areas to the south.

Source: Creed et al. (2019).

Deforestation of tropical forest could impact wind patterns and circulation of precipitation regionally and around the globe, with potential for impacts on water availability for agriculture (Figure 13) (Lawrence and Vandecar 2015; Avissar and Werth 2005; Werth and Avissar 2005; Medvigy et al. 2013; Lawrence and Vandecar 2015). Continental interiors hold some of the world’s most important agricultural areas. Without contributions to rainfall from forests, research suggests these downwind interiors may experience far less rain (Ellison et al. 2017). Likewise, deforestation also could affect precipitation in some of the world’s continental interior cities, which could present significant challenges for their water supply. Water-scarce regions, such as the dry regions of northeastern Africa where the Nile River is the main water source, are likely to be most affected by deforestation (Ellison 2018).

In particular, changing weather patterns due to deforestation of tropical forests could have a large impact on water availability for agriculture (Lawrence and Vandecar 2015). Fluctuations in climate can have a huge impact on agricultural productivity (Liang et al. 2016). Figure 13 describes the impacts of deforestation of tropical forests in different regions. Evidence also suggests that climate and precipitation are already more variable because of deforestation. Research typically models impacts using simulations:

• Within the Amazon Basin, forest loss is associated with reductions in rainfall (an average of 8 percent by 2050) in model simulations, according to a 2015 meta-analysis (Spracklen and Garcia-Carreras 2015).
• Modeling suggests that forest loss in the Amazon (Medvigy et al. 2013) and Central Africa (Akkermans et al. 2014) could reduce precipitation in the U.S. Midwest (Werth and Avissar 2005), with potential negative consequences on food production.
• Modeled changes resulting from deforestation in Southeast Asia appear to be smaller in magnitude but could reduce local precipitation in Southeast Asia as well as in Hawaii and the U.S. Pacific Northwest and even southern Europe (Avissar and Werth 2005).

Figure 13 | Simulated Total Deforestation of Major Forest Regions and the Effects on Global Precipitation Patterns

Note: Despite global rates of deforestation, total deforestation of the world’s major forest regions as simulated in this scenario is highly unlikely in reality.

Source: Authors. Adapted from Lawrence and Vandecar (2015).

These forests are in jeopardy. Since 2001, tree cover in the Congo Basin has decreased by more than 20 percent, mainly due to clearing for agriculture (Tyukavina et al. 2018). Southeast Asia is a global deforestation hotspot, with particularly high rates of habitat and biodiversity loss (Estoque et al. 2019). And, alarmingly, climate feedbacks between the Amazon Basin and Brazil’s nearby Cerrado forest and grassland ecosystems—currently subject to high rates of deforestation and agricultural conversion—may further threaten the precipitation patterns of both of these valuable regions (Spera et al. 2016).

Forest loss may accelerate the unpredictability of changes related to global warming. It is unlikely that forest protection or restoration can prevent or undo the changes to climate seen in recent decades, but it is worth stating that forest restoration is a good way to sequester more carbon in the landscape and offset other emissions. Yet because of their essential contributions to global climate as well as climate change mitigation efforts, the persistence of large forests may prevent further acceleration of global changes in climate and weather patterns. Conversely, increasing land cover change—including forest loss—may create greater uncertainty (Mahmood et al. 2014).

Caveats and considerations

Tropical forests may soon approach a tipping point where deforestation is occurring at such a high rate that the forests lose their capacity to recycle water effectively (Nobre and Borma 2009; Mahmood et al. 2014; Lovejoy and Nobre 2018). For example, if deforestation continues at present rates in the Amazon, 8 percent mean annual reductions in rainfall are expected by 2050 (Spracklen and Garcia-Carreras 2015). Consequently, its capacity to maintain continental and global water flows may erode.

Conserving forest is important for global water regulation, but it is less certain what the effects of large-scale reforestation or afforestation would be on regional evapotranspiration, precipitation patterns, and teleconnections (Mahmood et al. 2014). Large-scale afforestation of midlatitude regions, in particular, could have unintended consequences related to regional water availability and temperatures, resulting from changes in albedo (Swann et al. 2012). Protection of existing forests and restoration of previously forested lands should thus be prioritized over forest expansion.

To better understand the effects of forest changes to water availability and movement, more research is needed. Although the field of research relating to forests and water continues to grow rapidly, little research has been conducted on the effects of forest loss and degradation on hydrology in many parts of the world, including many low- and middle-income countries (Jones et al. 2020).

Concluding Thoughts

Although growing urban populations and shifting global climate patterns complicate efforts to provide clean and affordable drinking water, harnessing the power of forests in and around cities can help. Urban forests can reduce the burden of stormwater management on built infrastructure and insulate urban watersheds from the effects of pollution. In the watersheds surrounding cities, forests can protect water quality, buffer the risk of flooding, and ensure water availability from season to season. Vast tracts of intact forests—especially tropical rain forests—play an integral role in regional and global water movement and weather patterns. Yet global discourse and decision-making on protecting tropical forests does not yet sufficiently address their role in local, regional, and global hydrologic cycles (Ellison et al. 2017).

Cross-boundary water management is key to manage the interdependency of catchments and watersheds at multiple scales (Melo et al. 2021). Global cooperation is warranted to protect tropical forests because deforestation impacts agriculture, flood risk, and water availability around the world. To ensure that key agricultural regions—vital for urban sustenance—have adequate water supplies, cities will need to act to protect forests far beyond their boundaries.

Background

Around the world, cities are committing to bold action on climate change. Representing more than 700 million residents and one-fourth of the global economy, the dozens of members of the C40 Cities Climate Leadership Group (C40) have pledged to reduce GHG emissions in accordance with the goals of the Paris Agreement. Likewise, the ICLEI—Local Governments for Sustainability, which unites more than 1,700 cities, seeks to dramatically reduce its membership’s carbon emissions. Numerous similar initiatives—including the Climate Neutral Cities Alliance—exist to reduce carbon emissions in urban areas.

Cities are vulnerable to climate change. The effects of climate change—including heat waves, flooding, rising sea levels, and droughts—threaten the well-being of urban residents. Cities are hubs of innovation and economic activity and have a disproportionate concentration of both wealth and poverty residing in low-lying, coastal, and drought-prone areas (Rozenweig et al. 2010). Displacement due to sea level rise threatens to drive residents from some cities while causing influxes of rural climate refugees into other cities (Oppenheimer et al. 2019). Lower-income and marginalized residents are particularly vulnerable to the impacts of climate change, especially those in informal or unplanned settlements typical of rapidly growing cities. These threats are projected to continue to increase (Revi et al. 2014; Seto et al. 2014).

Urban residents’ concern about climate change is growing rapidly. City residents are demanding action from governments to take stronger, more decisive action on climate change. In September 2019, millions of city residents around the world took to the streets in protest, demanding action on climate change (Sengupta 2019; Taylor et al. 2019). Many urban-based climate action groups have started in recent years, and the demand for action from governments—including cities, by their residents—is growing and is likely to continue to grow as the impacts of climate change increase. While government action at all levels is important, more and more city governments are demonstrating their autonomy and sense of responsibility by taking action.

Reducing emissions within cities is the first important step, but forests can help cities go further. Cities consume more than 60 percent of the world’s natural resources (UN n.d.) and are responsible for approximately 75 percent of the world’s GHG emissions, when factoring in the goods consumed in cities but produced elsewhere (Seto et al. 2014). Decisions made in cities can have a large impact on climate change mitigation efforts. Unabated deforestation, especially in the tropics, may negate even the boldest reductions in emissions from fossil fuels (Griscom et al. 2017). To maintain a habitable climate, cities—the world’s largest pool of consumers—should examine how their consumption and actions affect the world’s forests at all levels and work to conserve and restore them.

Forests at all proximities to cities have a role. Increasing inner forests can have a mitigating impact on climate change in two key ways: sequestering carbon by urban trees and forests and lowering energy demands (and thereby energy-generated emissions) due to the temperature-moderating effects of the urban forests. Forests outside cities can help to mitigate climate change by absorbing and storing atmospheric CO₂. The IPCC’s 2019 Special Report on Climate Change underscores the urgency: without actions in the land sector, efforts to mitigate climate change are unlikely to succeed. To limit global warming to well below the 2°C target of the 2015 Paris Agreement, action on many fronts is needed (Griscom et al. 2017; Olsson et al. 2019).

About This Section

There are many ways that forests can help cities meet their climate change mitigation targets (Box 1). Forests can directly and indirectly alter atmospheric GHG concentrations, and they also influence other important biophysical processes that affect climate stability across scales.

The following section summarizes some of the most important ways that cities can mitigate global climate change through actions related to forests:

• Inner forests: Reduced energy emissions due to the temperature-moderating effects of the urban forests
• Inner forests: Carbon sequestration and storage by urban trees and forests
• Forests outside cities (near and far away): Global climate regulation and large-scale carbon sequestration and storage by forests, especially tropical forests

Forests inside Cities and Climate Change: Urban Cooling and Carbon Sequestration

Context

The urban environment creates challenging microclimates. Dense developments stifle airflow; steel, cement, and asphalt absorb heat from the sun and elevate city temperatures; and tall buildings create wind tunnels, causing discomfort in winter. When vegetation and open water are replaced with concrete, asphalt, and other materials, temperatures increase significantly (Mohajerani et al. 2017). These conditions can increase urban demand for energy for cooling (and in some cases, heating in winter), increasing emissions and further accelerating climate change.

Cities should consider strategies to limit or reduce the urban heat island effect as a way of reducing emissions. Cities are responsible for the bulk of the world’s GHG emissions (Seto et al. 2014). Transportation and industry play important roles, but maintaining habitable and comfortable indoor environments also contributes significantly. Emissions related to cooling are particularly noteworthy: urban heat islands can increase the demand for air-conditioning (Lundgren and Kjellstrom 2013) and air conditioner use—already responsible for 2 trillion kilowatt-hours of electricity annually, nearly 10 percent of global energy consumption—is expected to skyrocket in a warming world, especially in Asia (Dahl 2013; IEA 2018).

First, we examine the role of inner forests for microclimate regulation and carbon capture, following each with caveats and limitations. Then we do the same with forests outside cities.

Inner forests for microclimate regulation: What roles can trees and forests play?

Urban forests offer significant energy- and cost-saving benefits because they reduce extreme heat in summer, shade buildings, and in some settings buffer against strong winter winds. In this way, urban forests can help residents adapt to rising global temperatures—magnified by urban heat island effects—while simultaneously reducing urban emissions related to the heating and cooling of buildings.

By creating shade and lowering ambient air temperatures, trees can keep buildings cooler inside (Bowler et al. 2010a; Ko 2018). When trees shade buildings or evapotranspire, they reduce surface and ambient air temperatures, indirectly reducing the need to cool building interiors. On fossil fuel–powered electricity grids, a reduction in electricity use means a reduction in GHG emissions (Pataki et al. 2011; Roy et al. 2012; Mullaney et al. 2015). A 2018 systematic review of studies from North America suggests that cooling by trees can generate savings from 2.3 percent to as high as 90 percent of residential energy costs (Ko 2018), and another global review reported annual energy reduction benefits ranging from $2.16 to $64.00 per tree per year (Mullaney et al. 2015).

These reductions can produce significant cost savings. In the United States alone, urban forests reduce electricity use by 38.8 million megawatt-hours at a savings of $4.7 billion annually, with reductions in heating use estimated at 246 million British thermal units (savings of $3.1 billion annually) and avoided emissions savings valued at $3.9 billion annually (Nowak et al. 2017). Research from several Korean cities suggests that trees planted around multiresidential homes (totaling 32 percent of land used in Korean cities) reduced 0.367 million tCO₂ per year of emissions both directly and indirectly, offsetting the emissions of these homes related to heating and cooling by 3.3 percent, and the economic benefits of these trees related to carbon reductions and cost savings totaled $51 million per year (Jo et al. 2019).

When trees shield buildings from cold winds, they may also reduce the need to heat buildings. The evidence to support this, however, remains more limited. Cost savings for heating may range from 1 percent to 20 percent of energy costs for residential buildings in North America (Ko 2018). Reducing wind speeds may reduce winter heating costs but could conversely increase summer cooling costs in temperate climates (Ko 2018).

Inner forests for microclimate regulation: Caveats and considerations

Urban forests can provide meaningful microclimate moderation to reduce urban emissions, residential and commercial cooling and heating costs, and demand on energy generation facilities, all while creating other desirable cobenefits (Case Study 6). However, potential interactions should also be considered:

• The cooling effects of urban forests will vary between and within cities. Shading may produce only negligible reductions in indoor temperatures in areas where most residents inhabit tall multistory, multiunit residential buildings, as in many Chinese cities (Jim and Chen 2009). But in this context the cooling effects of evapotranspiration by trees can still be significant (Jim and Chen 2009).
• Tall urban trees can conflict with solar access for rooftop solar panels (Ko 2018). But this can largely be avoided with careful species selection and proper pruning (Ko 2018).
• In areas where water is scarce, the costs of irrigating urban trees may exceed the climate benefits provided (e.g., Pataki et al. 2011). In these contexts, selecting drought-resistant species with the ability to cool via shading may be especially important (Cameron and Blanuša 2016).
• Interactions with the built environment matter. For example, trees and shrubs very close to buildings may prevent the nighttime radiative cooling of buildings (Bowler et al. 2010a; Wang et al. 2014; Ko 2018). By blocking solar radiation in winter months, evergreen trees near buildings can actually increase energy demands (Lyytimäki and Sipilä 2009; Ko 2018).

Inner forests for carbon storage and sequestration: What roles can trees and forests play?

Canopy cover varies greatly among cities and is on the decline globally. Canopy cover varies with climate (Endreny et al. 2017) and between continents (Nowak and Greenfield 2020). Cities in forested regions typically have the greatest tree cover (averaging about 30 percent), followed by cities in grassland regions (18 percent) and cities in desert regions (12 percent; Nowak and Greenfield 2020). For example, the city of Atlanta contains 54 percent cover, compared to 8 percent in Cairo (Nowak et al. 2013; Endreny et al. 2017). Globally, urban tree cover is currently declining at a rate of 0.04 percent (about 40,000 ha) per year (Nowak and Greenfield 2020). The worst losses are occurring in Africa (1.5 percent lost per year) and modest gains are occurring in Europe (0.3 percent gained per year; Nowak and Greenfield 2020). Canopy cover is often used to estimate carbon storage in urban environments, and changes in canopy cover are used to estimate changes in carbon storage (Birdsey et al. 2019; Gibbs et al. 2022).

Total carbon storage and sequestration rates in urban forests vary with climatic and social contexts (Nowak and Crane 2002; Strobach et al. 2011; Nowak et al. 2013; Dobbs et al. 2014; Chen 2015). Cities with favorable growing seasons, robust urban forest management programs, or ample water supplies for vegetation may store more carbon than their counterparts lacking those characteristics. Variation also exists within individual cities. For example, tree-covered spaces such as urban parks and woodland patches typically store more carbon than street trees (Fares et al. 2017). More research is needed to understand carbon storage in cities globally, but some work has been conducted to date:

• In Beijing, street trees store an estimated 0.29 MtCO₂ and sequester an estimated 11,400 (+/- 6,600) tCO₂ annually (Tang et al. 2016), and that sequestered CO₂ is estimated to be equivalent to emissions of approximately 2,500 gasoline-powered passenger vehicles driven for one year.
• Urban forests in the United States store approximately 3,300 MtCO₂ and sequester 135 MtCO₂ annually (gross) in their aboveground and belowground biomass (Nowak and Greenfield 2018b), with that sequestration equivalent to emissions from energy use in more than 17 million homes in the United States.

Carbon stored in urban forests per unit area varies widely but is nearly always lower than in forests outside cities (Figure 14). Aboveground carbon density varies from about 3 tC per ha in Bangkok to about 34 tC per ha in Camden, United Kingdom, to about 32 tC per ha in Niamey, Niger (Intasen et al. 2016; Wilkes et al. 2018; Moussa et al. 2019). Carbon density in urban forests is consistently lower than carbon density of forests outside cities (Pan et al. 2011; Goldstein et al. 2020).

Aboveground carbon density (the amount of carbon per unit area in vegetation) has been measured for a number of urban forests; however, belowground carbon is less commonly measured. When the above- and belowground biomass for forests outside of cities is considered, these forests house far more biomass per unit area: 239–64 tC per ha for boreal forests and 242–52 tC per ha for tropical forests (Pan et al. 2011; Goldstein et al. 2020).

Figure 14 | Aboveground Carbon Density of Urban Forests in Selected Cities Compared with Various Faraway Forest Types

Note: For the most part, aboveground carbon density of urban forests in cities is only a fraction of the average aboveground carbon density of forests outside cities (Pan et al. 2011; Goldstein et al. 2020; Harris et al. 2021).

Source: Authors, with data from Nowak et al. (2013), Intasen et al. (2016), Tang et al. (2016), Tigges and Lakes (2017), Wilkes et al. (2018), Moussa et al. (2019), Goldstein et al. (2020), and Speak et al. (2020).

Inner forests for carbon sequestration and storage: Caveats and considerations

Can urban forests offset city emissions? The potential of restoring the world’s forests for climate change mitigation has gained prominence in the scientific literature (e.g., Bastin et al. 2019) and in innovative global initiatives such as the Bonn Challenge,¹⁹ Initiative 20x20,²⁰ the African Forest Landscape Restoration Initiative (AFR100),²¹ ECCA30,²² and Trillion Trees.²³ In some cases, cities are also increasing urban forests as a way to counterbalance carbon emissions from other sources and shrink the net municipal carbon footprint. Ambitious large-scale urban tree-planting campaigns are being supported and implemented around the world, as seen in the MillionTreesNYC project²⁴ or in Beijing’s planting of 50 million trees between 2012 and 2015 (Yao et al. 2019). Urban forests do store more carbon than many other urban land uses and provide abundant cobenefits. But expansions in urban tree canopy are unlikely to be an effective way for cities to meaningfully curb their net emissions for four reasons:

• Urban space for trees and forests is limited and costly. Although higher canopy cover could increase benefits related to carbon sequestration and storage (Endreny et al. 2017), pressure from development and infill can make large increases in canopy cover challenging or impossible. Urban infill does, however, provide other benefits to cities’ carbon footprints, as densification in walkable neighborhoods connected to public transit reduces emissions from private transportation.
• Urban forests can only sequester a tiny fraction—often less than half a percent—of overall city emissions (Case Study 7; Pataki et al. 2011). Research from diverse locations show similar numbers: Throughout China, the urban vegetation in 35 of its largest cities could offset only 0.33 percent of these cities’ total emissions (Chen 2015). In the United States, urban forests in cities throughout Florida mitigate between 1.8 and 3.4 percent of city emissions (Escobedo et al. 2010), whereas in Boston urban forests mitigate only 0.8 percent (Trlica et al. 2020). In Meran, Italy, forests sequester only 0.17 percent of city emissions (Speak et al. 2020). In Tabriz, Iran, urban trees currently mitigate 0.2 percent of the city’s emissions and could only be tripled to 0.6 percent over 20 years through an extensive city campaign of 150,000 new trees planted each year (Amini Parsa et al. 2019). Nonetheless, these emissions reductions can still translate into meaningful savings for cities—in the United States alone, the value of urban tree carbon sequestration is roughly $4.8 billion annually, and storage by urban trees is valued at roughly $119 billion (Nowak and Greenfield 2018b).²⁵
• Many urban trees require extensive, carbon-intensive care and maintenance during their life span. Planting, caring for, pruning, and removing urban trees using common fossil fuel–powered machinery releases GHG emissions (Nowak et al. 2002). Such emissions often outweigh the carbon sequestered by the tree, especially street trees and trees near buildings and infrastructure, which often require extensive maintenance. Many planted urban trees die young (Roman and Scatena 2011; Roman et al. 2014)—which could mean even more emissions related to removal and replacement. Urban vegetation may also be associated with biogenic emissions from soils and decomposition of plant material (see Velasco et al. 2016). Thus, trees planted in cities often only become carbon neutral decades after planting.
• Although urban trees grow faster, they also die younger than some of their rural counterparts, especially street trees (McPherson et al. 1994; Roman and Scatena 2011):
  • Urban trees often grow faster. Trees tend to receive more sunlight and warmth due to low-density spacing and the urban heat island effect (Zhang et al. 2004). Indeed, these favorable growing conditions can lead to relatively higher storage on a per-tree basis of urban trees compared to trees in rural forest stands—as much as four times greater (Nowak and Crane 2002). Urban tree growth can also be augmented by pruning, fertilizing, and irrigation. Good management of urban forests could promote additional carbon storage (Fares et al. 2017).
  • Urban trees face uniquely challenging conditions that can shorten their life span, including damage from construction, pollution, pests, and vandalism. Urban soils are often compacted and contaminated with salt, have low levels of nutrients, and unfavorable pHs (Velasco and Chen 2019).
  • The estimated average life expectancy of a street tree in temperate zones is 19–28 years, although trees in yards and parks tend to live longer (Roman and Scatena 2011).

Interventions in transportation or other sectors may be more impactful (Case Study 7). Because of the challenges that urban environments pose to tree growth, the necessary carbon inputs for many urban trees, and the premium placed on urban space, carbon sequestration by urban trees is not nearly as effective or cost-effective as sequestration in rural forests. Yet unlike most carbon sequestration and storage methods, urban trees can provide myriad cobenefits (Case Study 6).

In conclusion, reducing emissions by decarbonizing the energy and transportation sectors remains essential for cities serious about reducing their net carbon footprint. Although urban forests offset only a tiny fraction of total city emissions and the overall potential for carbon sequestration or local emissions offsetting is generally low (Pataki et al. 2011; Case Study 7), their potential for reducing urban heat islands and emissions from other sectors (such as the need for energy for air-conditioning) is considerable. Forests outside of cities, on the other hand, provide significant opportunities for cities looking to go further. Climate benefits achieved by preserving or restoring tropical forests far exceed the benefits that any amount of urban tree planting can provide.

Climate Change and Forests outside Cities, Near and Far

Context

Forest carbon storage and sequestration potential outside of cities far exceeds the potential within city boundaries. Globally, these forests cover approximately 30 percent (FAO 2018) of Earth’s land surface (down from an estimated 55 percent at the dawn of the agricultural revolution), whereas urban areas cover only around 3 percent in total (UNSD n.d.). Investing in forest conservation outside of cities also has many cobenefits enjoyed by all people, including conserving global biodiversity, ensuring availability of future medicinal compounds, and helping to maintain global hydrological cycles, as described in the other sections of this report.

Tropical forests hold massive amounts of carbon.²⁶ Globally, tropical forests store approximately 470 GtC, primarily in living plant tissue (Pan et al. 2011). The tropics also contain two particularly important ecosystems for carbon storage: tropical mangroves, which line the coasts of more than 110 tropical nations (FAO and UNEP 2020b), and forested peatlands, which are especially prevalent in Southeast Asia and have been subject to conversion to palm oil plantations in recent decades (Cazzolla Gatti et al. 2019). These forests store vast amounts of carbon, which is vulnerable to loss (Donato et al. 2011; Goldstein et al. 2020).

Tropical forests are being cleared at much higher rates than boreal and temperate forests, emitting vast amounts of carbon. If tropical deforestation were a country, it would rank third in annual CO₂e emissions, only behind China and the United States (Figure 15). From 2015 to 2020, an average of 9.3 million ha of tropical forest was lost annually, compared to 0.06 million ha of boreal forest and 0.31 million ha of temperate forest (FAO 2020). However, on a net basis, temperate forests actually gained 2.2 million ha per year from 2010 to 2015, boreal and subtropical forests had little net change, but tropical forests experienced a net loss of 5.5 million ha per year (Keenan et al. 2015; FAO 2016). According to data from Global Forest Watch, from 2002 to 2020 the extent of primary tropical humid forests decreased by 6.3 percent, with losses of 4.2 million ha—an area roughly as large as the Netherlands—in 2020 alone. Brazil, the Democratic Republic of the Congo, Bolivia, and Indonesia continue to see the largest losses of irreplaceable primary rain forest (Weisse and Goldman 2021).

Figure 15 | If Tropical Deforestation Were a Country It Would Have the Fourth Highest Carbon Emissions Globally

Notes: GHG = greenhouse gas; MtCO₂e = million metric tons of carbon dioxide equivalent.

Source: Authors. Based on data from Climate Watch (database), https://www.climatewatchdata.org/; and Pendrill, Persson, Godar, Kastner, Moran, et al. (2019).

The impact of cities on tropical forests around the world

Cities may cover only a tiny fraction of Earth’s surface, but they consume the majority of the world’s natural resources when factoring in the goods consumed in cities but produced elsewhere (UNSD n.d). Beef, soy, palm oil, wood fiber, coffee, and rubber are just a few examples of commodities extracted from forests or cultivated in formerly forested landscapes—often illegally—that have been associated with significant forest loss (Pendrill, Persson, Godar, and Kastner 2019).

Commercial production of key agricultural commodities—including soy, beef, and palm oil—is the largest contributor to tropical forest loss (Hosonuma et al. 2012; Seymour and Busch 2016; Weisse and Goldman 2021). Much of this goes to feed consumers in cities. Deforestation in the tropics to make space for agriculture, livestock, and establishing plantation forests is estimated to emit 2.6 GtCO₂ (about 0.71 GtC) per year—around 5 percent of 2017 global emissions (Pendrill, Persson, Godar, Kastner, Moran, et al. 2019).²⁷ Of this deforestation, roughly a quarter to a third is attributable to international demand for commodities; for example, when Brazilian beef is exported to Europe or the United States (Pendrill, Persson, Godar, and Kastner 2019; Pendrill, Persson, Godar, Kastner, et al. 2019). From 2001 to 2015, deforestation to make space for agricultural commodities was responsible for an estimated 27 percent of global tree cover loss (Curtis et al. 2018). Expansion of small-scale, often shifting agriculture, accounted for an additional 24 percent of global loss, and 93 percent of total tree cover loss in Africa (Figure 16; Curtis et al. 2018).

Figure 16 | Commodity-Driven Tree Cover Loss by Driver for the Period 2001–2018

Note: Certain types of deforestation may not be permanent—for example, forests may be able to grow back after a fire or following logging. But clearing for commodities represents a “permanent”’ transition from forest to nonforest land use, making it a much more significant source of climate-changing emissions. Within the context of this study, forest loss was categorized as shifting agriculture if the cell contained clearings that “showed signs of existing agriculture or pasture in most recent imagery as well as past clearings that contained visible forest or shrubland regrowth (gain) in historical imagery spanning the study period” (Curtis et al. 2018).

Source: Harris et al. 2020.

Beyond agricultural commodities, increased demand for timber or woody biomass for energy may also place pressure on tropical forests—now or in the future. Timber harvests can also lead to deforestation and ecological degradation, as when primary forests are replaced by fast-growing plantation forests, new logging roads are created, or forests are targeted by illegal logging (Shearman et al. 2012; Seymour and Busch 2016). Wood fuel is also implicated in the struggle to maintain tropical forest cover (Sassen et al. 2015; Pearson et al. 2017) and, as with other biofuels, can create land-use competition with food production at a global level, potentially jeopardizing a sustainable food future (Searchinger et al. 2018).

The linkage between deforestation and the urban consumption patterns that drive demand for these commodities reveals an important pathway for cities to reduce their carbon footprints. Avoiding deforestation is one of the most cost-effective ways to reduce emissions while conserving a carbon sink. Cities can act on this by practicing more sustainable sourcing of the commodities responsible for much of the world’s tropical deforestation, such as beef, soy, palm oil, coffee, and wood fiber; insisting that the countries those commodities come from stop deforesting land; and reducing the consumption of commodities such as beef. Because cities tend to use more resources than rural populations (Baabou et al. 2017) and are densely populated, changing urban consumption patterns can have a big impact on reducing deforestation (Defries et al. 2010). In the last decade, many multinational companies have committed to deforestation-free supply chains (Lyons-White and Knight 2018). Tropical timber, coffee, and chocolate can all be sourced in ways that do less harm to forests (Hylander and Nemomissa 2009; De Beenhouwer et al. 2013; Böhnert et al. 2016). Although deforestation-free sourcing has been implemented by some companies and at national levels, this strategy has yet to be widely adopted by cities. But cities can contribute meaningful action on this front, as evidenced by Oslo’s palm oil campaign and biofuel ban (Case Study 8). Promoting awareness is the first step cities can take towards these goals, as the World Wide Fund for Nature’s Earth Hour City Challenge has shown (Khan and Borgstrom-Hannson 2016).

When used in concert with conserving forests, forest restoration and integrating trees into farmland through agroforestry and silvopastoral systems can also serve as important tools for climate change mitigation. Conserving forests is a more effective, and more cost-effective, means of reducing the accumulation of carbon in the atmosphere (Box 1) than forest restoration alone. But as a complementary strategy, forest restoration often increases the carbon storage in forest ecosystems (Shimamoto et al. 2018). Land can be left to regrow forests on its own (Cook-Patton et al. 2020), whereas tree planting is important to reforest areas that are too degraded or severely disturbed to recover naturally, such as degraded pastureland and areas affected by catastrophic wildfires that destroy nearby sources of seed (Wilson and Rhemtulla 2016; Holl and Brancalion 2020). Where ecological conditions allow, letting forests regenerate naturally on previously forested land can regain some of their former functions in a cost-effective way (Crouzeilles et al. 2017; Cook-Patton et al. 2020). For example, there are currently 2.4 million square kilometers of secondary-growth forests in Latin America. If allowed to continue growing, these forests could sequester 8.48 GtC from 2008 to 2048—an amount equivalent to all emissions from fossil fuel use and industrial processes from countries in Latin America and the Caribbean from 1993 to 2014 (Chazdon, Broadbent, et al. 2016). Research suggests that if the full 350 million ha pledged for restoration under the Bonn Challenge were allowed to regenerate naturally, it could provide about 42 GtC storage (about three years of current global GHG emissions) by 2100, compared with 1 GtC storage if the same volume of land were turned into plantations (Lewis et al. 2019).

Caveats and considerations

Not all forests provide the same carbon benefits: forest biodiversity creates more reliable carbon sinks and a safer investment for cities.

• More biodiverse native forests tend to store more carbon than simplified/less biodiverse forests under similar climatic and geographic conditions (Cavanaugh et al. 2014; Poorter et al. 2015). This has been attributed to higher resource capture, more efficient resource use, and higher productivity (Poorter et al. 2015).
• Mixed-species plantations can store greater amounts of carbon than monoculture (Díaz et al. 2009; Piotto et al. 2010; Potvin et al. 2011; Huang et al. 2018; Jactel et al. 2018; Waring et al. 2020). Carbon storage can be further increased by incorporating species with desirable traits, such as nitrogen-fixing species (Jactel et al. 2018; Marron and Epron 2019).
• To offer long-term climate benefits, forests must be resilient. Biodiverse forests are likely to be more productive and offer more carbon benefits and other cobenefits due to increased resilience to disturbance and climate shocks (Liang et al. 2016; Jactel et al. 2018; Waring et al. 2020). But most planted forests in the tropics are planted with only one species, leaving them more vulnerable to disease and climatic disturbance (Payn et al. 2015; Seddon et al. 2019; Waring et al. 2020). Research shows that forests planted with mixed native species and mature native forests are more resilient. Whether planted, mature, or secondary, biodiverse forests are likely to be more productive. For example, intact tropical forests—which tend to be more biodiverse than degraded forests or monoculture plantations—create desirable traits by hosting nitrogen-fixing species (Jactel et al. 2018; Marron and Epron 2019) and establishing their own microclimates that reduce the risk of fire and protect them from droughts (Thompson et al. 2009).

With increasing climate uncertainty and risks as a result of climate change, it is not enough to maintain a certain area of forest; rather, maintaining forest quality and resilience will be essential to protecting forests to ensure they continue to store and sequester carbon.

Without immediate action to stop tropical deforestation and degradation, and encourage forest regrowth, these ecosystems could reach a “tipping point” where once-carbon-rich forests become drier savannah-like ecosystems (Lovejoy and Nobre 2018). Warming climates mean more drought and fires, which could double the area of land in the Amazon consumed by wildfires alone by 2050 (Brando et al. 2020). In a downward spiral, climate change harms tropical forests, inhibiting their ability to sequester carbon and releasing emissions that accelerate the rate of climate change (Baccini et al. 2017; Hubau et al. 2020; Anderegg et al 2020; Goldstein et al. 2020). When severely degraded or disturbed, forests may approach a tipping point, a threshold beyond which forest function deteriorates and becomes more vulnerable to human impact (Goldstein et al. 2020). The ability of tropical forests to sequester carbon in both Latin America and Africa is already being compromised due to degradation and the effects of climate change (Baccini et al. 2017; Hubau et al. 2020). Similarly, Harris et al. (2021) show that some of the largest tropical forests in the world are close to flipping from carbon sinks to carbon sources, with disastrous consequences for global CO₂ levels. Of the three largest tropical rain forests, only the Congo’s tropical forests remain a strong carbon sink, with the Amazon teetering on the edge of becoming a source and forests across Southeast Asia becoming a net source of carbon emissions over the past 20 years (Harris et al. 2021).

Achieving carbon-neutrality commitments will require cities to integrate forests and trees into climate strategies. Conserving and restoring forests are currently some of the only natural, proven, and potentially cost-effective solutions to sequestering carbon and achieving net-negative emissions. Several cities are also exploring a number of innovative (and contested) strategies to harness the climate mitigation potential of forests, each with their own caveats and considerations (Box 2).

Concluding Thoughts

Dramatic changes in key sectors are needed to reduce global emissions and atmospheric CO₂ emissions. Yet achieving these transformations in transportation, agriculture, or industry remains challenging—even politically contentious. Natural climate solutions can offer a broadly appealing and complementary pathway to avoid catastrophic damage from climate change and accrue cobenefits related to health and biodiversity.

Agile and wielding immense political power, cities are poised to be leaders in addressing climate change by reexamining their connections to forests. Although tropical forests may seem far removed from the activities of the city, consumption patterns in urban areas drive deforestation and degradation that releases massive amounts of carbon—and threaten our ability to avoid overshooting climate targets. Forests are the only natural, proven, and cost-effective carbon solution that can actually sequester carbon and produce negative emissions. And cities have the ability to protect and support these ecosystems, both directly and indirectly.

City actions that protect the world’s forests, especially tropical forests, can go a long way towards mitigating climate change. This commitment requires a multipronged approach that includes a shift towards sustainable, deforestation-free products and materials; shifting the diets of residents to more plant-based foods; and reducing food loss and waste. Forest-based approaches should not replace cuts to anthropogenic emissions—reducing emissions and sequestering carbon are both needed to meet global emissions reduction targets (Anderson, C.M., et al. 2019).

Background

Cities gain tremendous benefits from biodiversity (Box 3) inside and outside their boundaries (Figure 17). Biodiversity is a key feature of resilient ecosystems (Yadav and Mishra 2013), and cities rely on resilient systems for a wide range of services. Within cities, biodiversity can have positive impacts on mental health (Fuller et al. 2007; Wood et al. 2018). Around cities, biodiversity supports key regulating and provisioning ecosystem services, such as pollination (Cardinale et al. 2012; IPBES 2016; Alvarez-Garreton et al. 2019; Yu et al. 2019). Outside city boundaries, global biodiversity directly supports human health, food security, and climate regulation and provides the blueprints for new medicines (Chivian and Bernstein 2010; Hisano et al. 2018). The value of services from natural ecosystems, which rely on biodiversity to function, has recently been estimated at $44 trillion, or over half the global economy (World Economic Forum 2020).

Biodiversity is becoming a major topic in cities around the world. Activist groups, such as Extinction Rebellion, are demanding action to protect Earth’s species. Often, young and deeply engaged leaders are at the forefront of the charge, creating action plans and mobilizing political support and resources (Bagley 2019; Nwanevu 2019). Despite their distance from many of the world’s natural ecosystems, it makes sense that grassroots action is originating among city residents: cities have both a lot at stake and the strongest foothold to effect change in the cultures, regulatory frameworks, technologies, and market systems that are currently responsible for global biodiversity loss. The future of cities relies on a collective ability to keep natural ecosystems functioning. Cities contain highly concentrated populations that depend almost entirely on resources and ecosystems far outside their boundaries. Partly because of this, biodiversity is increasingly appearing on city agendas, although mainly at the inner forest level (Brende and Duque 2021).

But global biodiversity is rapidly declining. Because of the importance to human well-being everywhere, including within cities, multiple international agreements exist to support biodiversity conservation via sustainable development, including the Convention on Biological Diversity and the Intergovernmental Science-Policy Platform on Biodiversity and Ecosystem Services (IPBES n.d.). Yet despite these efforts, the world is already in the midst of the sixth “global extinction” (Kolbert 2014). Around 1 million species are at risk of going extinct, many within the next few decades (IPBES 2019), mainly from habitat loss and climate change. Up to 150 species are estimated to go extinct every day (CBD Secretariat 2007), and current extinction rates are 100–1,000 times greater than the “background” rate of extinction (Pimm et al. 2014; Ceballos et al. 2015). Unlike past mass extinctions, the current extinction event is being driven by humans, through habitat loss, climate change, overexploitation, and invasive species (Tilman et al. 2017; Mazor et al. 2018).

Reduced biodiversity could have widespread impacts on the functioning of ecological support systems on which cities rely (Ceballos et al. 2017; Tilman et al. 2017). When native biodiversity is lost, ecosystems often become more vulnerable to disturbance and become less reliable—and less effective—at providing vital services. Habitat fragmentation in highly biodiverse areas can even lead to spillover of pathogens from wildlife reservoirs to human hosts (Borremans et al. 2019; Evans et al. 2020). It is uncertain how much biodiversity loss can be sustained before ecosystems see major loss of function (Dirzo et al. 2014; Moore 2018).

Forests are bastions of biodiversity, and biodiverse forests also provide more reliable, plentiful benefits across health, water, and climate. Forests are estimated to hold well over 60 percent—to perhaps 90 percent—of Earth’s terrestrial biodiversity²⁸ (Erwin 1982; Wilson 1988; Reid and Miller 1989), and forest conservation is essential to maintaining the diversity of life on Earth (Wilson 1988; Brooks et al. 2006; Mittermeier et al. 2011). But forests are being rapidly cleared, and deforestation is a leading cause of global extinction (Tilman et al. 2017)—a widely reported estimate states that 135 species a day are lost through deforestation alone, but this is difficult to pinpoint as the total number of forest species and their ranges are unknown (Wilson 1988). In 2020, 12.2 million ha of tropical forest were lost, of which over a third—4.2 million ha—were in humid tropical primary forests, which are extremely important sources of biodiversity (Weisse and Goldman 2021). People in cities are responsible for an astounding 75 percent of tropical deforestation per year through their consumption. Their direct choices and indirect influence are key to conserving forest biodiversity globally and, with it, important benefits upon which they rely.

Maintaining urban forest biodiversity is increasingly appearing on urban agendas, but municipal policies and practices to protect forest biodiversity in forests outside their boundaries are rare.²⁹ In this section, we highlight nine key ways—based on the authors’ synthesis of the literature review—that forest biodiversity near and far supports cities and city residents—and, in turn, how cities can work to support and conserve global biodiversity.

Figure 17 | The Biodiversity Benefits of Forests at Three Levels

Source: Authors. Adapted from Cities4Forests n.d.a

Nine Things Cities Need to Know About Biodiversity

Cities benefit from biodiversity and can also support it. The following nine points outline how biodiverse forests are vitally important to cities and what benefits they deliver to cities (Figure 18).

Figure 18 | Nine Things Cities Need to Know About Biodiversity

Source: Authors.

1. Biodiverse forests provide more goods and services to cities

Biodiverse forests are more resilient and have higher ecosystem function—key for climate change mitigation, water purification and regulation, and maintaining other forest benefits over time.

Biodiverse forests produce and sustain more ecosystem services on which city residents rely (Fischer et al. 2006; Flynn et al. 2011; Cardinale et al. 2012; Oliver et al. 2015). People in cities rely on forests for a large suite of different services, including mental and physical health, clean water, and climate regulation on many scales. To provide benefits, forests must be able to persist and recover from changes in the environment, including storms, droughts, and a changing climate. Maintaining higher levels of biodiversity can help them do that. “Higher biodiversity can be thought of as biological insurance”: when an ecosystem has many species fulfilling similar roles, it can continue to function even if some of those organisms are lost because the roles overlap (Yachi and Loreau 1999; Brandon 2014, 3). Biodiverse forests have high function and high “resilience,” or the ability to resist and rebound from shock, especially in comparison to monoculture plantations (Holling 1973; Folke et al. 2004; Thompson et al. 2009; Isbell et al. 2011; Brandon 2014; Liu et al. 2018).

Resilience is especially important for delivering forest benefits to city residents in the long term. Resilient forests persist for longer time periods. In cities, planting and maintaining a diversity of trees can prevent widespread tree loss when a new pest or disease is introduced (Santamour 2004; Raupp et al. 2006; Guyot et al. 2016). For example, in the United States, the introduction of Dutch elm disease and the emerald ash borer decimated millions of elm and ash trees, with extensive losses in urban areas (Santamour 2004; Raupp et al. 2006). Larger urban trees provide greater benefits (e.g., shade and cooling), so structurally diverse forests (with large, old trees and small, young trees) can provide additional resilience against environmental threats. Biodiverse forests in and out of cities can better weather storms, species invasions, weather fluctuations, and often human disturbance (Fischer et al. 2006; Flynn et al. 2011; Cardinale et al. 2012; Oliver et al. 2015).

2. Biodiverse forests store more carbon, more reliably

Conserving forests with high native biodiversity is a climate-biodiversity win-win for cities looking to take action on either front.

Having cities invest in forests is vital to climate change mitigation efforts. Intact and native forests sequester more carbon, store carbon longer, and provide much greater biodiversity conservation benefits than degraded forest or monoculture plantations (Holl and Brancalion 2020; Watson et al. 2020). A greater diversity of species and functional traits leads to more thorough carbon capture and storage throughout the ecosystem (e.g., aboveground versus belowground carbon; Díaz et al. 2009; Seddon et al. 2020). The higher resilience of biodiverse forests makes them a more reliable carbon sink—especially in the face of climate change, which increases extreme weather events and the need for forests to adapt to changing conditions (Turner et al. 2009; Brandon 2014; Seddon et al. 2019). Cities looking for cost-effective ways to action on climate change should consider integrating intact, biodiverse forest conservation efforts outside of cities into their climate change agendas—especially when considering procurement and sourcing options.

3. Biodiverse, intact forests protect watersheds

Native, biodiverse forests in watersheds are more effective than planted monocultures at supplying key water resources to downstream cities (Box 4; Case Study 5; Alvarez-Garreton et al. 2019; Yu et al. 2019).

The structure, impact on soils, and greater resilience of native forests create better conditions for storing and filtering water and are more likely to persist than many alternative land uses and monoculture tree plantations. For example, in south-central Chile, converting native forest to pine plantations had a negative impact on water availability, resulting in reductions in runoff (Little et al. 2009) and streamflow in the summer dry season (Box 4; Lara et al. 2009). Conversely, increases in native forest cover were linked to increases in streamflow in the dry season, when water was most needed.

4. Biodiversity in the world’s forests provides the blueprints for new medicines and pharmaceuticals

Even though only a small percentage of Earth’s plants have been tested, medicines in wide use come from plants—many of which come from highly biodiverse tropical forests.

Medicinal compounds from forests are commonly used by city residents around the world. More than half of all commercial medicines are based on compounds derived from species in the wild (Figure 19; Chivian and Bernstein 2010). More than 28,000 plant species have been recorded as having a medicinal use (Allkin 2017), and an estimated 25 percent of modern medicines are derived from plants (Farnsworth and Morris 1976; Robinson and Zhang 2011).

Medicines derived from forest products include antibiotics, anticancer agents, anti-inflammatory compounds, and analgesics (Sen and Samanta 2015). Examples include morphine, aspirin, vinblastine (a lifesaving treatment for Hodgkin’s disease), and vincristine (which treats acute childhood leukemia; Chivian and Bernstein 2010). In the developing world, 70–95 percent of the population—including many people living in cities—rely on traditional medicines, such as herbal medicines derived from natural environments such as forests, for primary care. These medicines make up an $83 billion per year industry (Robinson and Zhang 2011).

Figure 19 | New Approved Drugs between 1981 and 2010

Notes: Twenty-two percent derived from natural product, 4 percent natural products, 15 percent biologics (derived from mammals), 6 percent vaccines, 29 percent synthetic, 24 percent from synthetic sources but modeled or mimicking a natural product (Newman and Cragg 2012). This means that 26 percent of drugs are either natural products or are directly derived from them. If including direct and indirect sources (and not including biologics and vaccines), 50 percent of drugs come from plants.

Source: Authors. Adapted from Newman and Cragg (2012).

And this is just the tip of the iceberg—fewer than 1 percent of plant species on Earth have been examined for medicinal potential (IUCN 2011). As forests—and tropical forests, in particular—house a disproportionate share of the world’s biodiversity, conserving forest is critical for future medical discoveries.

As the world’s biodiversity declines, opportunities to discover new medicinal compounds decrease. “As species vanish, so too does the health security of every human. Earth’s species are a vast genetic storehouse that may harbor a cure for cancer, malaria, or the next new pathogen—cures waiting to be discovered” (Mittermeier et al. 2011). A telling example comes from Australia. In 1980, two frog species were discovered in the rain forest with a unique reproductive strategy: they would ingest their own eggs to protect them and later regurgitate their young. A unique compound around the eggs prevented them from being digested—exactly the type of compound that would be useful in treating peptic ulcer sores on the stomach lining that cause burning pain. But before studies could be completed, both species went extinct due to habitat loss and other human activities (Chivian and Bernstein 2010). Peptic ulcers affect over 4 million people in the United States alone—and 1 in 10 people suffer from them (Harvard Health Publishing 2014). Extinctions like this happen more frequently than we would like to imagine (Wilson 1992). As forests are cleared, “hidden extinctions”—where undiscovered species disappear through extinction—reduce the biological bank that medicinal researchers have to draw from, and the possibilities for future medical advances.

5. Biodiverse forests support the world’s pollinators—and urban food supplies

Pollinators are considered essential for an estimated 35 percent of global food production (Klein et al. 2007). Many of these pollinators require native ecosystems—and biodiverse forests—to thrive.

Cities import 99 percent of their food—and are almost completely reliant on pollination services outside their boundaries. Within cities, pollination is important for urban trees, gardens, and so forth. But currently only an estimated 1 percent of global food production comes from urban agriculture³⁰ (Clinton et al. 2018), and urban croplands account for only 5.9 percent of total croplands globally³¹ (Thebo et al. 2014). Most cities rely almost entirely on agricultural lands outside of cities and import the majority of their food.

Global food production relies on both wild and managed pollinators. Seventy-five percent of the 115 leading global food crops depend, to some extent, on animal pollination, accounting for 35 percent of food produced globally (Klein et al. 2007). The Food and Agriculture Organization of the United Nations estimated that pollination services in the countries responsible for 60 percent of the world’s agricultural production (Australia, Austria, Belgium, Canada, Denmark, Finland, France, Germany, Greece, Ireland, Italy, Luxembourg, Netherlands, New Zealand, Portugal, Spain, Sweden, the United Kingdom, and the United States) were valued at between $20 and $35 billion—per year. Some estimates at the global scale put this value higher: one study³² estimated that all pollination services had a value of $153 billion for global agriculture in 2005 (Gallai et al. 2009). Diversity of both wild and managed pollinators is important for providing more stable and effective crop pollination (Brittain et al. 2013; IPBES 2016).

But the world’s pollinators are in trouble. Land-use change (including deforestation), pesticide use, climate change, and diseases and parasites are affecting pollinators around the world (Mburu et al. 2006; Vanbergen 2013; Potts et al. 2016; Sritongchuay et al. 2019; Frick et al. 2020). Wild pollinators, which include insects and bats, and are important for both crops and wild plants and are in decline (Biesmeijer et al. 2006; Potts et al. 2010; Vanbergen 2013; Martin 2015). Wild bees and butterflies are especially threatened (IPBES 2016). Beekeepers in the United States and Europe have also reported annual hive losses of 30–50 percent for the past 10 years (10 percent is considered normal; Grossman 2013; Martin 2015).

Forests, along with other natural ecosystems, directly enhance pollinator populations in both temperate and tropical regions (Öckinger and Smith 2007; Nicholls and Altieri 2013; Bailey et al. 2014). For example, the Brazilian Atlantic Forest supports pollination processes for valuable crops, including coffee (Hipólito et al. 2019). Native pollinators tend to increase with proximity to natural habitat (Kremen et al. 2004). In many contexts, agricultural landscapes with natural areas or remnants near fields have more pollinators and higher crop yields (Morandin and Winston 2006; Monasterolo et al. 2015; Cusser et al. 2016). For example, in Japan native forests were shown to support native bee pollinators, whereas plantations did not (Taki et al. 2011), and in China, majority monoculture stands had 49–91 percent fewer bee species than native forests (Hua et al. 2016). Conserving, restoring, and maintaining the biodiversity of native forests outside of cities is crucial for maintaining pollinator populations and therefore food security within cities (Krishnan et al. 2020).

Forests, too, require native pollinators to function and provide ecosystem services. Over 85 percent of wild flowering plants are animal pollinated (tropical species, 94 percent; temperate species, 78 percent; Ollerton et al. 2011; FAO and UNEP 2020b). In tropical forest environments, for example, where wind pollination is rare, flowering plants are almost exclusively pollinated by a wide variety of animal pollinators (Bawa 1990). Nonagricultural forest benefits are rarely included in global valuation of pollinator services but are essential for people everywhere, including city residents (Mburu et al. 2006). Pollinators also make forests more resilient by maintaining genetic diversity of plant species (FAO and UNEP 2020b; Krishnan et al. 2020). Plant and pollinator diversity are inextricably linked and are essential for the provision of a wide range of ecosystem services (Kearns et al. 1998; Ollerton 2017). Losing pollinators via the loss of forest biodiversity is a negative downward spiral with serious implications for forests and agriculture.

6. Protecting biodiverse forests can reduce risks of zoonotic and vector-borne diseases and pandemics

Tropical deforestation can increase the transmission of infectious diseases—including novel ones—to humans.

In 2020, the COVID-19 pandemic spread around the world, with profound social and economic consequences and devastating loss of life. In many nations, cities were the hardest hit. Like many emerging infectious diseases, researchers suspected the virus responsible (SARS-CoV-2) was animal borne (zoonotic), and that it may have jumped from bats, civets, or pangolins (Mallapaty 2020).

The novel coronavirus is not an outlier: 61 percent of infectious diseases and 75 percent of new and emerging pathogens originate in animals (Taylor et al. 2001; Karesh et al. 2012). Although many of these pathogens persist among animal hosts for ages, deforestation, environmental degradation, agricultural intensification, and increased human presence in biodiversity hotspots—especially in the tropics—can increase human-wildlife interactions and allow contagious viruses and bacteria to leap from animals to humans (Wolfe et al. 2007; Karesh et al. 2012; Jones et al. 2013; Borremans et al. 2019).

Deforestation may play a role in the spread of emerging infectious diseases as well as outbreaks of established vector-borne disease (Evans et al. 2020; Guégan et al. 2020):

• In West and Central Africa, clearing intact rain forest has been associated with Ebola virus outbreaks due to increased animal-to-human contacts, which promote the possibility for disease transmission (Olivero et al. 2017).
• Yellow fever has been linked to deforestation (Wilcox and Ellis 2006) because it increases ground-level activity of the virus’s vectors (Monath and Vasconcelos 2015).
• Deforestation has been tied to malaria incidence via mosquito abundance in Latin America (Guerra et al. 2006; Karjalainen et al. 2010), but not in Southeast Asia (Guerra et al. 2006) or Africa (Bauhoff and Busch 2020).
• Deforestation and habitat fragmentation are also implicated in the spread of Lyme disease: as biodiversity declines, animal hosts of ticks such as mice become overabundant (Allan et al. 2003; LoGiudice et al. 2003).

Evidence suggests that maintaining high levels of biodiversity can decrease transmission of some infectious diseases (Civitello et al. 2015). Preventing deforestation and minimizing environmental degradation—especially in biodiversity hotspots such as the world’s tropical rain forests—could play a role in preventing the next pandemic (Evans et al. 2020; UNEP 2020; Alimi et al. 2021).

7. Access to biodiverse nature in urban areas provides measurable benefits to urban residents

Biodiverse forests can provide more reliable and richer health benefits to urban residents.

Access to natural environments is linked to an impressive list of mental and restorative health benefits (Hartig et al. 2014). Nature generally implies some degree of native biodiversity and function. The few studies on nature and health that incorporate biodiversity often indicate positive relationships (or, in some cases, no effect; Fuller et al. 2007; Lai et al. 2018; Marselle et al. 2019; Ngheim et al. 2021; Wood et al. 2018). The quality and type of green space also matters; for example, a study in Australia showed that wooded areas provide more mental health benefits, and that access to nature—not just green space—is important (Astell-Burt and Feng 2019).

Urban forests can be the only source of nature for many city dwellers. For example, a survey of New York City park users in 2013–14 found that 50 percent of people who use city parks only experience nature in urban parks (Pregitzer et al. 2019). Maintaining high-quality natural areas within cities is key for many residents to access the health and other local benefits biodiverse forests provide.

Urban forests can also provide early childhood nature experiences—and may be the only source of them for many children in cities. Exposure to nature in childhood can have lasting impacts on an individual’s feelings towards the environment (Sampaio et al. 2018). Spending time in nature early in life is associated with pro-environmental behavior later in life in both developing and developed nations (e.g., Evans et al. 2018; Rosa et al. 2018). Time in nature can also be important for children’s development—but children are getting less and less of it, in part because of the loss or inadequate amount of natural, biodiverse areas in cities (Louv 2005).

Biodiversity in the urban forest contributes to the distinctive character of cities around the world and can help connect people to place and encourage ecotourism (Hausmann et al. 2016). For example, Rio de Janeiro is internationally known for its astounding biodiversity and nature in the city, which is a point of pride to city residents and a major attraction for visitors worldwide. Working together to restore ecosystems can also connect people to place as well as to each other (Higgs 2003).

8. Urban forests can house high biodiversity

Urban forests can be highly biodiverse, but they also tend to have more invasive species, “generalist” species, and fewer endemic species than rural forests in the same habitat type (Concepción et al. 2015; Ducatez et al. 2018; Borges et al. 2021).

Urban areas occur in many of the world’s most biodiverse landscapes. For example, 422 cities³³ are found in the world’s “hotspot” regions—areas of critical importance to biodiversity conservation with both high endemic biodiversity and extensive habitat loss (Seto et al. 2011; Weller et al. 2017). Cities are highly transformed environments, but many still support surprisingly high levels of biodiversity (Box 5). Their potential as migration corridors is also key for migratory species. In some cases, moderate levels of urbanization (e.g., lower-density settlements in suburbs, less homogeneity, larger and more evenly distributed green spaces) can even increase the biodiversity of certain groups, such as plants and certain bird species (Marzluff et al. 2001; Chace and Walsh 2006; McKinney 2008).

Urban forests often support lower biodiversity and fewer endemic species than forests outside of cities (Boxes 6 and 7). Despite the ability of some urban areas to support relatively high levels of biodiversity, these areas are often different from ecosystems found outside of cities. Urbanized areas often report lower species richness (total number of species) or species density (species per unit area) than nonurbanized areas (Marzluff et al. 2001; Chace and Walsh 2006; McKinney 2008; Aronson et al. 2014).

Cities often support different types of species, including more exotic and invasive species and fewer wildlife species, than nonurban areas (specifically animals with large ranges, highly specific habitat requirements, and large mammals; Adams 1994; Marzluff et al. 2001; Chace and Walsh 2006; McKinney 2008; Aronson et al. 2014). Non-native species are often intentionally planted, sometimes because they are well adapted to city conditions (Potgieter et al. 2017) but can spread into and threaten biodiversity in nearby forests. They also limit the opportunity to conserve locally endemic or other native species. Non-native, invasive species can be detrimental to ecosystem services, spread disease, produce allergens, or lead to “biotic homogenization,” where forests in different places become increasingly similar because common invasive species dominate at the expense of other species (Gaertner et al. 2017).

Both the size and connectivity of natural areas in cities are crucial for supporting urban forest biodiversity. A global meta-analysis showed that these two factors were more important than other biodiversity-friendly management techniques or the surrounding landscape, and that areas of more than 50 ha are often needed to conserve more vulnerable species (Beninde et al. 2015).

The case studies in Boxes 6 and 7 highlight the difference between biodiversity in some of the world’s best examples of biodiverse urban natural areas and the forests found outside of cities. Collectively, these studies illustrate that well-managed and cared-for urban forests can have high biodiversity and can protect threatened and/or endemic species. Nonetheless, they are unable to support all the species in a given area. Conservation efforts outside of cities are therefore essential for conserving global biodiversity.

9. Tropical forests hold the majority of Earth’s terrestrial biodiversity and are therefore essential to urban well-being and sustainability

Where should cities invest in global biodiversity? Global biodiversity conservation priorities based on different metrics consistently identify tropical forests as priorities. Because cities around the world directly impact tropical forests via their consumption, they are in a strong position to improve their own biodiversity impacts through local policies that reduce negative impacts or invest in conservation.

Tropical forests hold up to 90 percent of the world’s land-based species. The tropics cover about 40 percent of Earth’s surface but are home to over 90 percent of bird species and 75 percent of other groups, including mammals, freshwater fish, ants, and flowering plants. The species richness (total number of species) of mammals, birds, and plants increases consistently from the poles to the tropics (Barlow et al. 2018). Within the tropics, forests hold an enormous amount of this biodiversity—most (65–90 percent) of the world’s land-based biodiversity is found in tropical forests, which are far more biodiverse than temperate and boreal forests³⁴ (Wilson 1988; Reid and Miller 1989; WRI et al. 1992).

Cities looking to conserve global biodiversity need to look both inside and outside their boundaries. Efforts to conserve biodiversity that focus only on urban areas are limited by area, degree of habitat intactness, and—critically—their geographical location. The Amazon rain forest is estimated to contain 16,000 tree species. Canada and the United States combined are estimated to hold fewer than 650 but are approximately 3.6 times the size of the Amazon. Even more impressive is that this number—650 species—can be found in one hectare of tropical rain forest, indicating both the Amazon’s high level of species richness (Coley and Kursar 2014) and the potential return on investment for cities promoting biodiversity conservation in the tropics. This pattern holds true across multiple types of species as well as multiple tropical forests. Madidi National Park in Bolivia may be one of the most biodiverse areas in the world (WCS 2012; Brandon 2014). In contrast, the temperate Yellowstone National Park supports relatively high biodiversity for a temperate area but has only a fraction of the species (Figure 20; NPS 2019).

Figure 20 | A Comparison of the Species Found in Tropical Madidi National Park and Temperate Yellowstone National Park

Source:Authors. Adapted from data from WCS (2012) and NPS (2019).

The Amazon, Brazilian Atlantic Forest, Congo Basin, and other parts of Central Africa contain about 50 percent of the species on Earth in only 7.5 percent of its land area and have the highest species richness per unit area in the world (Jenkins et al. 2013). That is why most of the many methods to prioritize where to invest to conserve global biodiversity point to the tropics (Myers et al. 2000; Brooks et al. 2006).

Tropical forests are home to many endemic species (Figure 21). Endemic species are critical for global biodiversity conservation because they are more vulnerable to habitat destruction in a specific place. There are six times more endemic species in tropical areas than temperate ones (Barlow et al. 2018). Tropical mountains (notably the Andes) and islands in particular are home to species found nowhere else (Myers et al. 2000; Kier et al. 2009).

Most global biodiversity hotspots are in the tropics. Thirty-five global biodiversity hotspots have been identified using species “irreplaceability” (endemism) and “vulnerability” (the chance that they stand of being wiped out due to habitat loss³⁵; Mittermeier et al. 2011). These hotspots cover 2.3 percent of the world’s land area, down from 15.9 percent originally, due to extensive habitat destruction in the last century. Yet they still house an astounding proportion of the world’s species (Figure 22): the tropical Andes alone has 30,000 plant species, of which 15,000 are endemic (Mittermeier et al. 2011). Nearly all 35 hotspots are in the tropics and subtropics, and all are either completely or partially forest biomes.

Figure 21 | Relative Forest Biodiversity Significance, 2018

Notes: Forest biodiversity significance is based on the “distribution of forest mammal, bird, amphibian, and conifer tree species” (Hill et al. 2019). Darker areas show higher significance values; white areas are not classified as forest.

Source: Hill et al. (2019).

Figure 22 | Percentage of the World’s Terrestrial Vertebrates and Plants Endemic to the 35 Global Biodiversity Hotspots

Source: Authors. Adapted from Mittermeier et al. (2011).

Caveats and Considerations

Measuring biodiversity is difficult and inexact. This applies to estimates of global or regional biodiversity and global extinction rates. These numbers give a range for the vastness of biodiversity and changes over the decades but are imprecise by nature. However, they still have value and are instrumental in communicating the general trends; for example, that extinction rates are increasing or that there is higher biodiversity in the tropics, which indicate when and where action is needed.

Biodiverse forests are important for their untapped medicinal potential, but this can lead to instances of traditional medicinal knowledge being stolen or co-opted. Bioprospecting—“the exploration of biodiversity for new biological resources of social and economic value”—can be especially extractive in the context of pharmaceuticals (Beattie et al. 2011). Although the importance of biodiversity for new discoveries should not go unacknowledged, neither should the contributions of local and Indigenous peoples to building this knowledge and their rights to these resources. When exploring these topics, cities should ensure that there is equitable benefit sharing and proper recognition of intellectual property.

Debate remains around the concept that higher biodiversity decreases the risk of infectious diseases, a hypothesis known as the dilution effect (Salkeld et al. 2013; Civitello et al. 2015). When applied generally, the link between biodiversity and infectious disease transmission is less conclusive, oftentimes mitigated by the specific disease’s system. However, the argument that deforestation and forest degradation contribute to the spread of infectious diseases is largely separate from the dilution effect and more strongly supported, though these mechanisms could reinforce each other. The conclusion that protecting biodiverse forests to decrease the spread of infectious diseases therefore still stands.

Some argue that biodiversity has inherent and cultural value. While not quantifiable in the same manner as the topics focused on in this section, there are arguments that biodiversity is important intrinsically and should therefore be protected. Sometimes this is described as “existence value,” which does not require any direct use for there to be value but instead simply the knowledge of its existence is enough.

Concluding Thoughts

Conserving biodiversity is critical to provide essential services that city dwellers rely on every day. Biodiverse forests are more resilient, and thus a more reliable source of forest benefits. Inside the city, biodiverse forests support improved mental health, pollination, and, in some cases, tourism. Forest biodiversity outside of cities supports services that we rely on every day, including food security (via pollination and global rainfall patterns), medicinal resources and research, climate change mitigation, and even buffering against future pandemics.

Conserving tropical biodiversity can be a double (or triple) win for cities because the world’s most biodiverse forests are also critical for providing other benefits (carbon sequestration; global hydrology cycles). Cities could consider investing in biodiverse forests to which they are connected by flows, such as migratory bird routes, rainfall patterns, or in areas of high carbon density.

Although cities are far removed from the world’s most biodiverse forests, they have a big impact on these environments and can play a critical role in conserving them. When it comes to biodiversity conservation, tropical forests are key. Conserving native, intact forests outside of cities in the tropics is the most important measure that cities can take because these forests contain far higher levels of native biodiversity than most secondary forests, temperate forests, and urban tropical forests. They are also especially important for conserving endemic species (Holl and Brancalion 2020). People in cities consume the majority of the world’s goods and commodities, many of which currently harm diverse forests—but this impact could be greatly reduced through better sourcing and changing consumption habits. Cities can also conserve biodiversity with their boundaries, including by maintaining and expanding diverse natural areas throughout cities.

Introduction

Decades of research and on-the-ground outcomes show the untapped potential of forests to meet city needs and aspirations.

As cities face the dual challenges of growing populations and accelerating climate change, they need scalable solutions that can be implemented at relatively low cost. This report shows that forests at all three levels—inner, nearby, and faraway—can provide essential services to city residents, including improved human health, increased water security, improved microclimate regulation, climate protection, and biodiversity conservation. Forests often provide these services at lower cost than traditional infrastructure alone and can be integrated into cost-saving hybrid systems (Browder et al. 2019). Cities can use their plans, policies, and actions to harness the power of forests to build thriving, resilient communities, creating a mutually beneficial relationship between cities and forests.

What can cities do to realize the myriad benefits that trees and forests can provide them?

Our analysis has identified actions cities can take, and our synthesis of the literature and interviews categorized these under five thematic categories:

1. 
   Measurement and monitoring
2. 
   Planning
3. 
   Partnerships
4. 
   Finance
5. 
   Markets

Under each of these categories are “no regrets” measures that allow a city to take immediate action to leverage the power of inner, nearby, or faraway forests to help meet their goals and serve their residents. Although these recommendations are not exhaustive, they provide direction for cities to take tangible action. Underpinning these measures are a set of guiding principles (Box 8)—determined by the authors based on the latest primary literature—that apply to all recommendations. These actions are intended to help deliver the benefits described in this report and raise awareness of how critical forests are to thriving, resilient cities (Box 9). The recommendations and categories of action are summarized in Figure 23.

 

Box 9 | Cities4Forests: A Vision for the Future

Current City Challenges/Status Quo			Future Directions
City planners may see urban trees and forests as luxuries, “nice to have,” or sometimes liabilities	→		Urban nature seen as essential infrastructure, integral to human well-being and resilient, equitable, and habitable cities and appropriately supported by urban policy, finances, and culture
Research on urban forest expansion only uses “canopy cover” for planning and assessment	→		Urban forest expansion uses diverse metrics for high-quality natural forests and trees to deliver most-needed services in targeted areas, with community input
Urban forest management is siloed among city agencies; little communication across different departments	→		Increased coordination, cooperation, and partnership between city agencies, city residents, and private industry to support forests
City governments see nearby and watershed forests as outside the city’s purview, jurisdiction, and/or concern	→		Nearby and watershed forests seen as vital to cities, supported by city regulations and incentives in collaboration with rural and municipal stakeholders outside urban limits
Consumers see forests as resources to be managed primarily for wood and paper products	→		Forests are living ecosystems managed for multiple benefits simultaneously: nontimber forest products, carbon sequestration, other climate and hydrological services, human heath, cultural services, and native biodiversity
City governments and residents see forest conservation as an impediment to growth	→		Forest conservation, restoration, and sustainable management can lead to new jobs, resilient cities, forests and landscapes, and many other benefits to the city
City governments and residents do not understand the linkage between “faraway” tropical forests and urban well-being	→		Protection and restoration of tropical forests seen as essential by city governments to efforts to maintain a livable Earth and preserve biodiversity for future generations
City governments perceive that tropical and intact forests are outside the scope of city action	→		City governments and residents empowered to take an active role in tropical forest conservation and restoration via procurement, climate action, and other direct support

Source: Authors.

Actions for City Practice and Policy

Suggested policy actions are divided by level—inner, nearby, and faraway forests—and the thematic category that each action addresses.

Inner forests: Urban trees, parks, green infrastructure, and natural areas

With planning and long-term investment, inner forests can provide multiple social, health, environmental, and economic benefits to cities and their residents. Most of the recommendations at the inner forest level can be implemented through existing city agencies, departments, and their close implementing partners directly. Making training and education available to staff of multiple city agencies will empower them to do so. In particular, having staff trained in arboculture is essential: trees are community assets that require specific skills and expertise to help them thrive in urban environments. Interagency collaboration and partnership with urban residents and stakeholder groups is also important for achieving outcomes.

Measurement and monitoring: Inner forests

• Map, inventory, and monitor your city’s urban forest. Develop an urban tree cover baseline and land cover map as a first step towards planning and monitoring urban forests. Evaluate key urban environmental challenges—such as heat islands, urban flooding, and lack of green space (WRI Mexico 2016; Singapore-ETH Centre n.d.)—that could be improved through better forest management, and use available socioeconomic information to ensure equitable distribution of the benefits of trees to all city residents. For example, North Macedonia’s Skopje Green Cadaster³⁶ involves a comprehensive mapping, recording, and cataloging of all public green zones in the city, including every bush and tree. Identifying areas where trees and forests are not present is also important to identify needs and opportunities (UNDP North Macedonia n.d.).
• Quantify the benefits of urban trees, especially iconic and mature ones. A range of tools can be used to quantify the benefits of existing trees, including large and mature ones that often have disproportionate cultural or ecological value (Pool et al. 2022; Box 10). This analysis can be used to garner political and resident support as well as guide investments in (for example, by justifying local budget decisions) and management of urban forests. For example, i-Tree Eco³⁷—an online tool developed by the U.S. Forest Service to quantify and value ecosystem services provided by trees—was recently adapted, translated, and launched for Mexican cities, allowing cities across Mexico to quantify the extent and composition of urban forests and calculate their ecosystem services and monetary value. Findings from the Chapultepec Forest, a vast urban forest in Mexico City, are available via an interactive map for resident education and engagement, influencing public awareness and building the case for preserving urban forests (SEDEMA n.d.).³⁸

• Align forest monitoring metrics with city goals. Measuring the right thing is critical to achieving and assessing specific benefits. Canopy cover is often measured to assess urban forests within cities, but it does not provide comprehensive information for all forest benefits. Using proper metrics to evaluate and track urban forests can help align goals, actions, and outcomes. In addition to canopy cover, focus on other forest qualities that improve forest function, such as biodiversity, location, forest type, dominant species, quality of the understory vegetation, location, size, and other metrics that align with the goals for these forests (Pregitzer et al. 2019).
• Articulate clear goals. These are a few examples:
  • Increase forest canopy by X percent. The appropriate canopy cover targets will depend on what is appropriate for local conditions (e.g., climate; natural tree canopy cover outside the city) and should be used with additional targets—such as species diversity or a mix of stand ages—to ensure forest diversity and health. In Barcelona’s Trees for Life: Master Plan for Barcelona’s Trees,³⁹ the city set a target to increase tree canopy by 5 percentage points for a total of 30 percent (Barcelona City Council 2017).
  • Ensure every resident has green space within half a mile of home. Cities are seeking to achieve equitable access to green space. For example, Vancouver’s Greenest City 2020 Action Plan⁴⁰ pledged that all Vancouver residents would live within a five-minute walk of a park, greenway, or other green space by 2020 (City of Vancouver 2012).
  • Reduce heat island or stormwater threats by X percent. Cities are establishing targets that address climate risks such as flooding, drought, and heat. In Australia, Western Sydney’s Turn Down the Heat: Strategy and Action Plan⁴¹ has set targets to reduce average peak ambient temperatures in the city by 1.5°C through greening and cool materials strategies by 2023 (WSROC 2018).

Planning: Inner forests

• Develop an urban forest management plan. The plan should be scientifically informed, based on nationally or internationally recognized standards, take climate change into consideration, and prioritize native species. It should also encourage education, outreach, and, if possible, support or training for private landowners—the majority landowners in many cities. Some cities have created dedicated urban forestry departments to take charge of this, but others coordinate this effort between multiple municipal agencies. Developing a robust urban forest management plan can help maximize ecosystem services from the urban forest, which includes street trees, parks, natural areas, and other urban forests (Box 11).
• Designate land specifically for natural areas. Even small patches of forests—in parks, vacant lots, along roadways, and in industrial areas—can provide access to nature in under-served areas. For example, the Miyawaki method, in which diverse plantings of trees and shrubs are used to create microforests, has been used to create local access to nature and increase urban biodiversity in many cities (Nargi 2019).

• Create connectivity. Connecting landscapes and urban green spaces supports plant and animal populations, including songbirds and pollinators. Corridors of diverse native forest can facilitate the movement of pollinators, support wildlife, provide space to alleviate stress, increase foot and bike commuting, and reduce exposure to pollution for residents. Successful examples of green corridor projects include the Medellín Green Corridors (UNEP 2019) and the Barcelona Green Corridor Network (O’Sullivan 2017).

Partnerships: Inner forests

• Seek out organizations conducting innovative work on inner forests and propose partnership models to share resources and track outcomes. Work with credible, long-standing organizations with the capabilities and resources to conserve, create, and manage parks and other natural areas. Working with these organizations can help to both manage forests and build community-based stewardship. For example, the Natural Areas Conservancy⁴² in New York City is a formalized partnership that focuses on maintaining and improving the city’s vast natural areas network, integrating the city’s needs with the conservation benefits these areas provide, and providing extensive community outreach.
• Cultivate interagency and cross-jurisdictional collaboration. Managing forests for multiple benefits that span different city agencies (including health, water, forestry, environment, and parks/recreation) can provide more benefits from the same amount of resources. Different agencies are also responsible for delivering and managing urban forestry, parks and open space, and green infrastructure in cities. The Joint Benefits Authority⁴³ is an example of a new mechanism that will allow multiple departments within a city to jointly plan, implement, and finance these types of transformative projects by quantifying the range of benefits that cross agency mandates (Box 12).

Finance: Inner forests

• Explore diverse, long-term financing mechanisms to manage, protect, and expand urban forests. Innovative financing tools include the following:
  • Green bonds and climate bonds fund projects that have positive environmental and/or climate impacts through the use of proceeds or asset-linked bonds. The Netherlands issued one of the world’s largest green bonds in 2019 (about $6.8 billion) to finance natural infrastructure solutions crucial for protecting its low-lying regions from sea level rise (Anderson, J., et al. 2019).
  • Pay for performance environmental impact bonds (also known as pay for success bonds and social benefit bonds) allow private investors to fund specific interventions and earn a return based on performance (i.e., paying for results rather than services). In 2019 Atlanta announced a $14 million impact bond for private investors to finance innovative green infrastructure projects to address critical flooding and water quality issues, reduce stormwater runoff, and enhance the quality of life in certain neighborhoods (Water Finance & Management 2019). Investors are paid back as the green infrastructure “performs” by reducing the impacts of stormwater flooding—such as damage to public infrastructure, private houses, and people’s lives—thereby saving the city money related to clean up costs.
  • Community-based public-private partnerships between local governments and private entities align the interests of public, private, and community stakeholders around common goals. In 2020, the Milwaukee Metropolitan Sewerage District launched to capture rainfall runoff and prevent downstream flooding and sewer system contamination issues (MMSD 2020). The partnership will identify priority areas for green infrastructure based on the ability to support program goals, such as reducing overflow volumes, reducing localized flooding, and improving water quality. It reduces the risk for taxpayers as the private entity partner (a design engineering firm) is paid based on performance (i.e., the volume of water attained).
  • Tree-planting funds collect funds from taxes and stormwater fees. In Madison, Wisconsin, the city council has adopted a special charge—collected as part of the Madison Water Utility’s municipal services bill—to support its growing urban forestry program and protect the vital services that the city’s urban forest provides (City of Madison n.d.).
  • Tree banks collect funds from public and private developers when trees are removed and their replacement value (in terms of the ecosystem services they were providing) cannot be achieved; they also support replacements in other places throughout the city.
  • Mitigation fees, such as those adopted by Maryland’s Montgomery County, require that development activities regulated by the county’s Tree Canopy Law mitigate their impacts by planting shade trees on sites where building disturbance occurs or pay the equivalent fees into the county’s Tree Canopy Conservation Account (Montgomery County Government 2017).
  • Integrate forests into city environmental compliance plans. Philadelphia’s Green City, Clean Waters program (PWD 2011) integrated green and gray solutions based on a triple bottom line approach (Green 2013) that is already paying off (Hess 2019).
  • Incentivize city residents to support trees and forests through tax reductions. For example, residents could be incentivized to plant trees for green stormwater infrastructure on private property via reduced stormwater fees (Berland et al. 2017). San Francisco’s Urban Watershed Stewardship Grant supports similar community-based projects managing stormwater and greening the city (SFPUC n.d.).

Markets: Inner forests

• Develop a wood waste reuse program. Rather than disposing of waste from street and yard trees in landfills, municipalities can develop wood waste reuse programs. Dead trees can become wood chips or fuel or salvaged for timber or architectural purposes. For example, Baltimore has implemented a wood reuse program, the Baltimore Wood Project (Room & Board 2018), which salvages wood from demolished buildings and street trees to repurpose them into furniture and other household items, creating jobs and reducing waste (Juno and Hines 2019).

Nearby Forests: Watershed and Recreation Areas around Cities

Cities can work with other levels of government and agencies to support the conservation, sustainable management, and restoration of nearby forests; many world-class examples exist of cities working to support nearby forests. Since most nearby forests fall outside city agency jurisdiction, partnership and collaboration with state, provincial, and federal government agencies, landowners and managers, and watershed stakeholders will be necessary for recommendation implementation.

The Better Forests, Better Cities publication reviewed the latest research on the effects of forests at three levels (inner, nearby, and faraway) on cities and their residents. The report summarizes the findings of research gathered through a series of systematic “reviews of reviews” (surveys of published review papers; e.g., van den Bosch and Sang [2017]) and scoping literature reviews complemented by “snowballing” (reviewing reference lists and/or expert recommendation), reviews of the primary literature, and literature recommended by topical experts, conducted for each of the four main sections: health and well-being, water, climate, and biodiversity.

The body of relevant work in each of these section topics spans multiple decades and encompasses an array of disciplines. Many topics were thus well suited to using the “review of reviews” method, which we found by developing a list of key search terms and performing a series of searches in scholarly databases (see individual sections for details). Throughout the publication, the formal review process was supplemented with primary literature, reports and gray literature, consultations with and recommendations from topical experts (see details of people consulted for each section below), and from the amassed experience of WRI and Pilot Projects in implementing various city-related projects (including Cities4Forests; UrbanShift;⁵² Wood at Work;⁵³ Urban Water Resilience Initiative;⁵⁴ the Global Commission on Adaptation,⁵⁵ specifically the cities and NBS tracks; Brooklyn Bridge Forest;⁵⁶ and various other projects through WRI’s Ross Center for Sustainable Cities,⁵⁷ Water Program,⁵⁸ and Forests Program⁵⁹) and their discussions and engagements with city representatives over the years. These findings have been used in the report as brief in-text illustrations and in-depth case studies to exemplify forest-related ecosystem services and their nuances, highlight success stories, portray other important ideas, and fill gaps in knowledge where insufficient reviews were available. Drafts of each section were also reviewed by experts in the respective fields prior to the formal review process.

Health and Well-Being

To equip urban leaders with an overview of the immense array of information connecting forests to human health and well-being, we conducted a systematic review of reviews—including peer-reviewed syntheses, meta-analyses, and summary reports in gray literature—identified using multiple databases. We supplemented our findings with empirical research from individual cities to provide additional context and geographic representation. Because human health and well-being research that focuses specifically on forests remains limited, we broadened our scope from urban forests and trees to include urban green space, green infrastructure, and urban nature in some portions of this section to provide a more comprehensive overview where forest-specific science was lacking; this shift in emphasis is indicated in the corresponding report text when applicable.

We began by conducting a systematic literature review of existing review papers, including other literature reviews, meta-analyses, and gray literature, later supplemented with additional information from primary sources.

We began a systematic literature review by identifying relevant search terms and seminal works in consultation with topic experts, including Dr. Kathleen Wolf⁶⁰ and Dr. Dexter Locke.⁶¹ After the initial list was created, exploration of existing reviews and reviews of reviews led to the addition of many terms. The search terms were designed to identify review papers that explored forests, urban areas, and at least one issue of social, physical, mental, or economic health and well-being simultaneously (Box A1).

Using a systematic review of three databases (Scopus, Web of Science, and PubMed), as well as Google Scholar, we identified peer-reviewed literature and other publications (e.g., book chapters and summary reports). The first phase of the systematic search returned 1,953 results, supplemented by the first 200 results from two Google Scholar searches (for a total of 2,353). During the first phase, we scanned titles and abstracts to determine relevance. During the second phase, following removal of duplicates, 384 full texts were reviewed. A small number of publications could not be accessed and were thus excluded. A total of 146 peer-reviewed articles, book chapters, and reports met inclusion criteria (i.e., written in English; needed to be a systematic review, meta-analysis, or narrative review; addressed one of the main research questions). In addition to the results of the systematic review, 36 publications identified by snowballing were included. Thus, in total, 182 texts were initially reviewed in full for inclusion in this publication. The returned documents represented a broad variety of disciplines, including urban forestry, landscape planning, environmental health, epidemiology, psychology, and political ecology.

In areas of interest where few or no review articles exist, we consulted relevant empirical studies in the primary literature (nonreview papers), identified via scholarly databases, review of reference lists, and additional recommendations from internal and external experts, including Elleni Ashebir,⁶² Dr. Beatriz Cardenas,⁶³ Dr. Jessica Seddon,⁶⁴ Dr. Theodore Eisenman,⁶⁵ Dr. Viniece Jennings,⁶⁶ Dr. Nick Hewitt,⁶⁷ and Dr. David Rojas-Rueda.⁶⁸

As a relatively young field, few studies on the specific health benefits of urban forests exist. Many of the reviews we identified referenced the same seminal studies (e.g., Ulrich 1984 or Kuo 2003). Similarly, many narrowly focused review articles (e.g., reviews of forest bathing) survey and dissect the same small body of literature. Aware of this potential for bias, we consciously sought to minimize repetition of these findings in our report.

To understand potential biases in the research of the 182 texts identified in the original systematic review, we recorded the location of the organization with which the first author of a publication was affiliated. Most of the first authors on the publications originated from North America, Europe, and Australia (Figure A1), which reflects the general pattern of urban ecosystem service research originating primarily in the global North (Haase et al. 2014).

Figure A1 | Geographic Locations of Primary Authors of Publications Reviewed During the Original Systematic Review (according to Institutional Affiliation)

Source: Authors. Adapted from Haase et al. (2014).

Water

To understand the connections between forests, cities, and their water supplies, we first conducted a scoping review of reviews, later supplemented with findings from empirical studies and reports. A comprehensive discussion of the vast literature on the relationship between forests and hydrological cycles (e.g., Guswa et al. 2020) at local and global scales is beyond the scope of this publication. Instead, we provide an overview of key points of interest for cities, including the effects of urban forests on stormwater and flooding, the importance of forests in maintaining healthy watersheds, and the emerging research on the global interconnections between large, intact forests and water.

As with the health and well-being section, to identify relevant search terms for our scoping review, we consulted experts at WRI (Suzanne Ozment,⁶⁹ Todd Gartner,⁷⁰ Paige Langer,⁷¹ and Sara Walker⁷²) and Conservation International (Aarin Gross⁷³ and Robin Abell⁷⁴). The initial list was created by combining forest terms, review terms, city terms, and water terms (such as stormwater, drought, flood, and water quality; Box A2). The results from the initial searches using forest terms, review terms, and city terms were complemented by relevant papers that had been identified to inform the broader literature search and from the suggestions of topical experts from WRI and other organizations. As with the health and well-being section, review of primary literature was used as necessary to supplement and illustrate trends, generalizations, and caveats and considerations.

Climate

To explore the connection between climate change mitigation and forests, we conducted two reviews for the climate section: a systematic review of reviews on forests outside cities and a review of reviews and empirical studies on forests inside cities, as the latter is an emerging field with few reviews available.

To identify relevant search terms, we consulted experts within WRI (Frances Seymour,⁷⁵ David Gibbs,⁷⁶ Nancy Harris,⁷⁷ Alexander Rudee⁷⁸) and externally (David Nowak⁷⁹). The initial list combined forest terms, review terms, and carbon and climate terms (Box A3). A secondary search using forest terms, review terms, and city terms yielded few results and encouraged researchers to pursue a different methodology to assess the role of forests inside cities on climate mitigation.

We tested the initial list of search terms for forests outside cities on Scopus and Web of Science. Similar to the health and well-being search, we simplified the forest terms, removing references to “ecosystem services” and “nature-based solutions” that greatly increased the number of reviews and were not as directly focused on trees or forests.

For forests outside cities, we conducted a systematic review of reviews on the Web of Science and Scopus databases as well as Google Scholar to identify peer-reviewed literature and other publications relevant to our research topic. The search returned 1,123 results from Web of Science and 854 from Scopus, in addition to the first 100 results from two Google Scholar searches (for a total of 2,177). During the first phase, we scanned titles and abstracts to determine relevance. During the second phase, following removal of duplicates and inclusion of snowballed articles, 410 full texts were flagged for review. A total of 27 peer-reviewed articles, book chapters, and reports met inclusion criteria (i.e., written in English; needed to be a systematic review, meta-analysis, or narrative review; addressed one of the main research questions). We then supplemented our review of these findings with additional recommendations from other colleagues and experts.

For forests inside cities, we conducted a scoping literature review of studies related to forest carbon storage and cooling benefits. Because carbon storage, carbon sequestration, and cooling/avoided emissions are typically classified as ecosystem services, many studies relevant to this section had already been identified in the systematic review conducted for the health and well-being section. We drew from these works and supplemented with additional exploration of the primary literature and of existing reviews.

To provide a comparison of urban forest carbon density per hectare with that of forests outside cities, we used data from seven peer-reviewed publications that were identified in our reviews on carbon storage inside cities that cover a range of climates and geographies. Six of the peer-reviewed studies provided citywide averages (Intasen et al. 2016; Moussa et al. 2019; Speak et al. 2020), and one study provided a national average for the United States (Nowak et al. 2013). (The researchers did not include data from Kumasi, Ghana, where the citywide average was 228 tC per ha, as this data point was considered to be an outlier; see Nero et al. [2018]). These data points for forests inside cities were compared to averages of carbon density in temperate, tropical, and boreal forests outside of cities, using ranges estimated from Pan et al. (2011) and Goldstein et al. (2020).

Biodiversity

To understand the connections between forests, cities, and city water supplies, we conducted a review of the ways that forests at all levels may support biodiversity using an initial list of search terms (Box A4). Each subtopic covered an extensive body of literature, and so by necessity a more general literature review approach was employed rather than a more systematic review of reviews.

Biodiversity often appeared in the searches for the preceding three sections (for example, 56 articles returned for the health and well-being search address some aspect of biodiversity). These papers were reviewed and summarized in the biodiversity section. Additional subtopics of interest identified by the authors through previous experience working with cities and research from preceding sections were covered via a scoping “review of reviews” search, and cases and empirical work were included to fill gaps or to develop fields of research where few or no review papers had been published. Several important sources were found through references from other papers or reviews and experts (Robin Chazdon⁸⁰ and Patricia Balvanera⁸¹) were consulted regarding seminal works on many of the topics.

Case studies on urban forest biodiversity were chosen based on preexisting knowledge of world-renowned urban forests and availability of information. To compare biodiversity in urban areas with areas outside cities, areas outside of the urban bounds were chosen based upon availability of data, proximity to the urban area (to maintain similarity of biome), and size (as close to urban forest area as possible). Specific searches were conducted to provide comparable species richness information for forested areas inside and outside of cities, and sources included peer-reviewed journal articles, gray literature, species lists reported by government or park web resources, and publicly available databases.

Recommendations for Policy and Action

Our recommendations in this section are derived in equal part from direct and indirect suggestions made by authors of the articles reviewed for the four main sections, and from engagements with city representatives (through project implementation, at conferences and during workshops, and through formal and informal discussions) and the experience that the Cities4Forests team has accumulated over the years from implementing forest-related projects with cities, including through the development of our Cities4Forests Toolbox⁸² and two learning guides focused on decision-makers, “Urban Forests for Healthier Cities: Policy, Planning, Regulations, and Institutional Arrangements” (Juno and Virsilas 2019) and “Social Equity Considerations for Cities’ Decision Making Related to Inner, Nearby, and Faraway Forests” (Trivedi et al. 2020), which represent the culmination of additional research on existing urban forest policy environments and consultation with experts and practitioners. We also relied on the experience of a team of colleagues who work on issues related to forests in cities, namely Todd Gartner, Terra Virsilas,⁸³ Lisa Beyer,⁸⁴ James Anderson,⁸⁵ Lizzie Marsters,⁸⁶ Suzanne Ozment, Ayushi Trivedi,⁸⁷ Natalie Elwell,⁸⁸ and Frances Seymour, to develop recommendations and general guidance based on best practices and lessons learned.

Recommendations were developed for several areas of policy and action, including measuring and monitoring, planning, partnerships, finance, and markets. For each forest level, we developed recommendations under each type of recommendation (for example, we outlined specific actions that cities could take to identify financing opportunities for inner forest initiatives). Communication was included as a cross-cutting theme for all forest levels.

Gaps and Limitations of the Methodology

The body of evidence exploring the roles that forests inside and outside of cities play in supporting our four topic areas of focus is expansive and rapidly growing. As a result, our reviews may not reflect some of the most recent developments in these areas. Language barriers and publishing biases may have also presented geographical bias in the reviews. To attempt to remedy this issue, we specifically sought to include findings from primary literature and highlight case studies from under-represented areas in the supplemental stages of our reviews.

Despite these limitations, we believe these reviews provide policymakers; city leaders; practitioners from civil society, community-based, and nonprofit organizations that work hand in hand with cities; and researchers with a broad, interdisciplinary overview of current research connecting forests and trees to the health and well-being of city residents and to cities’ goals related to water, climate change mitigation, and biodiversity preservation.

Abhijith, K.V., P. Kumar, J. Gallagher, A. McNabola, R. Baldauf, F. Pilla, B. Broderick, S. Di Sabatino, and B. Pulvirenti. 2017. “Air Pollution Abatement Performances of Green Infrastructure in Open Road and Built-Up Street Canyon Environments: A Review.” Atmospheric Environment 162 (August): 71–86. https://doi.org/10.1016/j.atmosenv.2017.05.014.

Adams, L.W. 1994. Urban Wildlife Habitats: A Landscape Perspective. Minneapolis: University of Minnesota Press. https://www.upress.umn.edu/book-division/books/urban-wildlife-habitats.

Afelt, A., R. Frutos, and C. Devaux. 2018. “Bats, Coronaviruses, and Deforestation: Toward the Emergence of Novel Infectious Diseases?” Frontiers in Microbiology 9 (April): 702. https://doi.org/10.3389/fmicb.2018.00702.

Ahern, M., R.S. Kovats, P. Wilkinson, R. Few, and F. Matthies. 2005. “Global Health Impacts of Floods: Epidemiologic Evidence.” Epidemiologic Reviews 27 (1): 36–46. https://doi.org/10.1093/epirev/mxi004.

Akbari, H., D.M. Kurn, S.E. Bretz, and J.W. Hanford. 1997. “Peak Power and Cooling Energy Savings of Shade Trees.” Energy and Buildings 25 (2): 139–48. https://doi.org/10.1016/S0378-7788(96)01003-1.

Akbari, H., M. Pomerantz, and H. Taha. 2001. “Cool Surfaces and Shade Trees to Reduce Energy Use and Improve Air Quality in Urban Areas.” Solar Energy 70 (3): 295–310. https://doi.org/10.1016/S0038-092X(00)00089-X.

Akkermans, T., W. Thiery, and N.P.M. Van Lipzig. 2014. “The Regional Climate Impact of a Realistic Future Deforestation Scenario in the Congo Basin.” Journal of Climate 27 (7): 2714–34. https://doi.org/10.1175/JCLI-D-13-00361.1.

Albaugh, J.M., P.J. Dye, and J.S. King. 2013. “Eucalyptus and Water Use in South Africa.” International Journal of Forestry Research 2013: 1–11. https://doi.org/10.1155/2013/852540.

Alfsen, M. n.d. “The Day the Norwegians Rejected Palm Oil and Deforestation.” Rainforest Foundation Norway. https://www.regnskog.no/en/long-reads-about-life-in-the-rainforest/the-day-the-norwegians-rejected-palm-oil-and-deforestation-1. Accessed April 14, 2021.

Alimi, Y., A. Berstein, J. Epstein, M. Espinal, M. Kakkar, D. Kochevar, and G. Werneck. 2021. Report of the Scientific Task Force on Preventing Pandemics. Boston: Harvard Global Health Institute and the Center for Climate, Health, and the Global Environment, Harvard T.H. Chan School of Public Health. https://cdn1.sph.harvard.edu/wp-content/uploads/sites/2343/2021/08/PreventingPandemicsAug2021.pdf.

Allan, B.F., F. Keesing, and R.S. Ostfeld. 2003. “Effect of Forest Fragmentation on Lyme Disease Risk.” Conservation Biology 17 (1): 267–72. https://doi.org/10.1046/j.1523-1739.2003.01260.x.

Allkin, B. 2017. “Useful Plants—Medicines: At Least 28,187 Plant Species Are Currently Recorded as Being of Medicinal Use.” In State of the World’s Plants 2017, edited by K.J. Willis. London: Royal Botanic Gardens, Kew. http://www.ncbi.nlm.nih.gov/books/NBK464488/.

Alvarez-Garreton, C., A. Lara, J.P. Boisier, and M. Galleguillos. 2019. “The Impacts of Native Forests and Forest Plantations on Water Supply in Chile.” Forests 10 (6): 473. https://doi.org/10.3390/f10060473.

Amini Parsa, V., E. Salehi, A.R. Yavari, and P.M. van Bodegom. 2019. “Analyzing Temporal Changes in Urban Forest Structure and the Effect on Air Quality Improvement.” Sustainable Cities and Society 48 (July): 101548. https://doi.org/10.1016/j.scs.2019.101548

Anderegg, W.R.L., A.T. Trugman, G. Badgley, C.M. Anderson, A. Bartuska, P. Ciais, D. Cullenward, et al. 2020. “Climate-Driven Risks to the Climate Mitigation Potential of Forests.” Science 368 (6497): eaaz7005. https://doi.org/10.1126/science.aaz7005.

Anderson, C.M., R.S. DeFries, R. Litterman, P.A. Matson, D.C. Nepstad, S. Pacala, W.H. Schlesinger, et al. 2019. “Natural Climate Solutions Are Not Enough.” Science 363 (6430): 933–34. https://doi.org/10.1126/science.aaw2741.

Anderson, J., T. Gartner, A. Mauroner, and J. Matthews. 2019. “Conservation Finance Takes Off as the Netherlands Issues One of the Largest Green Bonds Ever.” Insights (blog), June 21. https://www.wri.org/insights/conservation-finance-takes-netherlands-issues-one-largest-green-bonds-ever.

Anderson, J., J.R. Pool, S. Ummu Haniy, H. Evers, and P. Narayanan. 2021. “Cities Are Surprising Leaders in Forest Conservation.” Insights (blog), September 22. https://www.wri.org/insights/ways-cities-help-forest-conservation.

Antonelli, M., G. Barbieri, and D. Donelli. 2019. “Effects of Forest Bathing (Shinrin-Yoku) on Levels of Cortisol as a Stress Biomarker: A Systematic Review and Meta-analysis.” International Journal of Biometeorology 63 (August). https://doi.org/10.1007/s00484-019-01717-x.

APA (American Planning Association). 2015. “Green City, Clean Waters: Philadelphia’s 21st Century Green Stormwater Infrastructure Program.” https://www.planning.org/awards/2015/greencity.htm.

Aram, F., E. Solgi, E. Higueras García, A. Mosavi, and A.R. Várkonyi-Kóczy. 2019. “The Cooling Effect of Large-Scale Urban Parks on Surrounding Area Thermal Comfort.” Energies 12 (20): 3904. https://doi.org/10.3390/en12203904.

Aronson, M.F.J., F.A. La Sorte, C.H. Nilon, M. Katti, M.A. Goddard, C.A. Lepczyk, P.S. Warren, et al. 2014. “A Global Analysis of the Impacts of Urbanization on Bird and Plant Diversity Reveals Key Anthropogenic Drivers.” Proceedings of the Royal Society B: Biological Sciences 281 (1780): 20133330. https://doi.org/10.1098/rspb.2013.3330.

ASLA (American Society of Landscape Architects). 2016. “2016 ASLA Professional Awards: Bishan-Ang Mo Kio Park.” https://www.asla.org/2016awards/169669.html.

Astell-Burt, T., and X. Feng. 2019. “Association of Urban Green Space with Mental Health and General Health among Adults in Australia.” JAMA Network Open 2 (7): e198209. https://doi.org/10.1001/jamanetworkopen.2019.8209.

Austin, K.F. 2021. “Degradation and Disease: Ecologically Unequal Exchanges Cultivate Emerging Pandemics.” World Development 137 (January): 105163. https://doi.org/10.1016/j.worlddev.2020.105163.

Avissar, R., and D. Werth. 2005b. “Global Hydroclimatological Teleconnections Resulting from Tropical Deforestation.” Journal of Hydrometeorology 6 (2): 134–45. https://doi.org/10.1175/JHM406.1.

Baabou, W., N. Grunewald, C. Ouellet-Plamondon, M. Gressot, and A. Galli. 2017. “The Ecological Footprint of Mediterranean Cities: Awareness Creation and Policy Implications.” Environmental Science & Policy 69 (March): 94–104. https://doi.org/10.1016/j.envsci.2016.12.013.

Baccini, A., W. Walker, L. Carvalho, M. Farina, D. Sulla-Menashe, and R.A. Houghton. 2017. “Tropical Forests Are a Net Carbon Source Based on Aboveground Measurements of Gain and Loss.” Science 358 (6360): 230–34. https://doi.org/10.1126/science.aam5962

Bagley, K. 2019. “From a Young Climate Movement Leader, a Determined Call for Action.” Yale Environment 360, November 7. https://e360.yale.edu/features/from-a-young-climate-movement-leader-a-determined-call-for-action.

Bai, X., I. Nath, A. Capon, N. Hasan, and D. Jaron. 2012. “Health and Wellbeing in the Changing Urban Environment: Complex Challenges, Scientific Responses, and the Way Forward.” Current Opinion in Environmental Sustainability 4 (4): 465–72. https://doi.org/10.1016/j.cosust.2012.09.009.

Bailey, S., F. Requier, B. Nusillard, S.P.M. Roberts, S.G. Potts, and C. Bouget. 2014. “Distance from Forest Edge Affects Bee Pollinators in Oilseed Rape Fields.” Ecology and Evolution 4 (4): 370–80. https://doi.org/10.1002/ece3.924.

Baldauf, R. 2017. “Roadside Vegetation Design Characteristics That Can Improve Local, Near-Road Air Quality.” Transportation Research Part D: Transport and Environment 52 (May): 354–61. https://doi.org/10.1016/j.trd.2017.03.013.

Baldauf, R., and D. Nowak. 2014. “Vegetation and Other Development Options for Mitigating Urban Air Pollution Impacts.” In Global Environmental Change, edited by B. Freedman, 479–85. Dordrecht: Springer Netherlands. https://doi.org/10.1007/978-94-007-5784-4_23.

Barcelona City Council. 2017. Trees for Life: Master Plan for Barcelona’s Trees 2017–2030. Barcelona: Ecology, Urban Planning, Infrastructures, and Mobility Area, Barcelona City Council. https://ajuntament.barcelona.cat/ecologiaurbana/sites/default/files/Pla-director-arbrat-barcelona-ENG.pdf.

Barlow, J., F. França, T.A. Gardner, C.C. Hicks, G.D. Lennox, E. Berenguer, L. Castello, et al. 2018. "The Future of Hyperdiverse Tropical Ecosystems." Nature 559 (7715): 517–26. https://doi.org/10.1038/s41586-018-0301-1.

Barwise, Y., and P. Kumar. 2020. “Designing Vegetation Barriers for Urban Air Pollution Abatement: A Practical Review for Appropriate Plant Species Selection.” Climate and Atmospheric Science 3 (12). https://doi.org/10.1038/s41612-020-0115-3.

Bastin, J.-F., Y. Finegold, C. Garcia, D. Mollicone, M. Rezende, D. Routh, C.M. Zohner, and T.W. Crowther. 2019. “The Global Tree Restoration Potential.” Science 365 (6448): 76–79. https://doi.org/10.1126/science.aax0848.

Bauhoff, S., and J. Busch. 2020. “Does Deforestation Increase Malaria Prevalence? Evidence from Satellite Data and Health Surveys.” World Development 127 (March): 104734. https://doi.org/10.1016/j.worlddev.2019.104734.

Bawa, K.S. 1990. “Plant-Pollinator Interactions in Tropical Rain Forests.” Annual Review of Ecology and Systematics 21 (1): 399–422. https://doi.org/10.1146/annurev.es.21.110190.002151.

Beattie, A.J., M. Hay, B. Magnusson, R. De Nys, J. Smeathers, and J.F.V. Vincent. 2011. “Ecology and Bioprospecting.” Austral Ecology 36 (3): 341–56. https://doi.org/10.1111/j.1442-9993.2010.02170.x.

Beckett, K.P., P.H. Freer-Smith, and G. Taylor. 1998. “Urban Woodlands: Their Role in Reducing the Effects of Particulate Pollution.” Environmental Pollution 99 (3): 347–60. https://doi.org/10.1016/S0269-7491(98)00016-5.

Beninde, J., M. Veith, and A. Hochkirch. 2015. “Biodiversity in Cities Needs Space: A Meta-analysis of Factors Determining Intra-urban Biodiversity Variation.” Ecology Letters 18 (6): 581–92. https://doi.org/10.1111/ele.12427.

Berland, A., S.A. Shiflett, W.D. Shuster, A.S. Garmestani, H.C. Goddard, D.L. Herrmann, and M.E. Hopton. 2017. “The Role of Trees in Urban Stormwater Management.” Landscape and Urban Planning 162 (June): 167–77. https://doi.org/10.1016/j.landurbplan.2017.02.017.

Berry, R., S.J. Livesley, and L. Aye. 2013. “Tree Canopy Shade Impacts on Solar Irradiance Received by Building Walls and Their Surface Temperature.” Building and Environment 69 (November): 91–100. https://doi.org/10.1016/j.buildenv.2013.07.009.

Bhattacharjee, K., and B. Behera. 2018. “Does Forest Cover Help Prevent Flood Damage? Empirical Evidence from India.” Global Environmental Change 53 (November): 78–89. https://doi.org/10.1016/j.gloenvcha.2018.09.004.

Biesmeijer, J.C., S.P.M. Roberts, M. Reemer, R. Ohlemüller, M. Edwards, T. Peeters, A.P. Schaffers, et al. 2006. "Parallel Declines in Pollinators and Insect-Pollinated Plants in Britain and the Netherlands." Science 313 (5785): 351–54. https://doi.org/10.1126/science.1127863.

Birdsey, R.A., N. Harris, D. Lee, and S. Ogle. 2019. “USCP—Appendix J: Forest Land and Trees.” US Community Protocol, April 16. https://us-protocol.pubpub.org/pub/v732gbdy/release/1.

Blue Forest Conservation. n.d. “About the Forest Resilience Bond.” https://www.blueforest.org/forest-resilience-bond. Accessed June 14, 2020.

Blum, A.G., P.J. Ferraro, S.A. Archfield, and K.R. Ryberg. 2020. “Causal Effect of Impervious Cover on Annual Flood Magnitude for the United States.” Geophysical Research Letters 47 (5): e2019GL086480. https://doi.org/10.1029/2019GL086480.

Böhnert, T., A. Wenzel, C. Altenhövel, L. Beeretz, S.S. Tjitrosoedirdjo, A. Meijide, K. Rembold, and H. Kreft. 2016. “Effects of Land-Use Change on Vascular Epiphyte Diversity in Sumatra (Indonesia).” Biological Conservation 202 (October): 20–29. https://doi.org/10.1016/j.biocon.2016.08.008.

Bonnesoeur, V., B. Locatelli, M.R. Guariguata, B.F. Ochoa-Tocachi, V. Vanacker, Z. Mao, A. Stokes, and S.-L. Mathez-Stiefel. 2019. “Impacts of Forests and Forestation on Hydrological Services in the Andes: A Systematic Review.” Forest Ecology and Management 433 (February): 569–84. https://doi.org/10.1016/j.foreco.2018.11.033.

Borges, P.A.V., R. Gabriel, and S. Fattorini. 2021. “Biodiversity Erosion: Causes and Consequences.” In Life on Land: Encyclopedia of the UN Sustainable Development Goals, edited by W. Leal Filho, A.M. Azul, L. Brandli, A. Lange Salvia, and T. Wall. Cham, Switzerland: Springer. https://doi.org/10.1007/978-3-319-95981-8_78.

Borremans, B., C. Faust, K.R. Manlove, S.H. Sokolow, and J.O. Lloyd-Smith. 2019. “Cross-Species Pathogen Spillover across Ecosystem Boundaries: Mechanisms and Theory.” Philosophical Transactions of the Royal Society B: Biological Sciences 374 (1782): 20180344. https://doi.org/10.1098/rstb.2018.0344.

Bowler, D.E., L. Buyung-Ali, T.M. Knight, and A.S. Pullin. 2010a. “Urban Greening to Cool Towns and Cities: A Systematic Review of the Empirical Evidence.” Landscape and Urban Planning 97 (3): 147–55. https://doi.org/10.1016/j.landurbplan.2010.05.006.

Bowler, D.E., L.M. Buyung-Ali, T.M. Knight, and A.S. Pullin. 2010b. “A Systematic Review of Evidence for the Added Benefits to Health of Exposure to Natural Environments.” BMC Public Health 10 (1): 456. https://doi.org/10.1186/1471-2458-10-456.

Boyd, W., C. Stickler, A.E. Duchelle, F. Seymour, D. Nepstad, N.H.A. Bahar, and D. Rodriguez-Ward. 2018. “Jurisdictional Approaches to REDD+ and Low Emissions Development: Progress and Prospects.” Working Paper. Washington, DC: World Resources Institute.

Bradshaw, C.J.A., N.S. Sodhi, K.S.-H. Peh, and B.W. Brook. 2007. “Global Evidence That Deforestation Amplifies Flood Risk and Severity in the Developing World.” Global Change Biology 13 (11): 2379–95. https://doi.org/10.1111/j.1365-2486.2007.01446.x.

Bradshaw, C.J.A., and I.G. Warkentin. 2015. “Global Estimates of Boreal Forest Carbon Stocks and Flux.” Global and Planetary Change 128 (May): 24–30. https://doi.org/10.1016/j.gloplacha.2015.02.004.

Brando, P.M., B. Soares-Filho, L. Rodrigues, A. Assunção, D. Morton, D. Tuchschneider, E.C.M. Fernandes, M.N. Macedo, U. Oliveira, and M.T. Coe. 2020. "The Gathering Firestorm in Southern Amazonia." Science Advances 6 (2): eaay1632. https://doi.org/10.1126/sciadv.aay1632.

Brandon, K. 2014. “Ecosystem Services from Tropical Forests: Review of Current Science.” Center for Global Development Working Paper 380. Washington, DC: Center for Global Development. https://doi.org/10.2139/ssrn.2622749.

Bratman, G.N., C.B. Anderson, M.G. Berman, B. Cochran, S. de Vries, J. Flanders, C. Folke, et al. 2019. “Nature and Mental Health: An Ecosystem Service Perspective.” Science Advances 5 (7): eaax0903. https://doi.org/10.1126/sciadv.aax0903.

Braubach, M., A. Egorov, P. Mudu, T. Wolf, C. Ward Thompson, and M. Martuzzi. 2017. “Effects of Urban Green Space on Environmental Health, Equity and Resilience.” In Nature-Based Solutions to Climate Change Adaptation in Urban Areas: Linkages between Science, Policy and Practice, edited by N. Kabisch, H. Korn, J. Stadler, and A. Bonn, 187–205. Cham, Switzerland: Springer International. https://doi.org/10.1007/978-3-319-56091-5_11.

Brauman, K.A., G.C. Daily, T.K. Duarte, and H.A. Mooney. 2007. “The Nature and Value of Ecosystem Services: An Overview Highlighting Hydrologic Services.” Annual Review of Environment and Resources 32 (November): 67–98. https://doi.org/10.1146/annurev.energy.32.031306.102758.

Bray, D., and A. Velazquez. 2009. “From Displacement-Based Conservation to Place-Based Conservation.” Conservation and Society 7 (1): 11. https://doi.org/10.4103/0972-4923.54791.

Brende, B., and I. Duque. 2021. “A New Initiative Could Make Cities More Biodiverse: Here’s How.” Davos Agenda 2021 (blog), January 27. https://www.weforum.org/agenda/2021/01/biodivercities-nature-initiative-transform-cities/.

Brittain, C., C. Kremen, and A.-M. Klein. 2013. “Biodiversity Buffers Pollination from Changes in Environmental Conditions.” Global Change Biology 19 (2): 540–47. https://doi.org/10.1111/gcb.12043.

Brooks, T.M., R.A. Mittermeier, G.A.B. da Fonseca, J. Gerlach, M. Hoffmann, J.F. Lamoreux, C.G. Mittermeier, J.D. Pilgrim, and A.S.L. Rodrigues. 2006. “Global Biodiversity Conservation Priorities.” Science 313 (5783): 58–61. https://doi.org/10.1126/science.1127609.

Browder, G., S. Ozment, I. Rehberger Bescos, T. Gartner, and G.-M. Lange. 2019. Integrating Green and Gray: Creating Next Generation Infrastructure. Washington, DC: World Bank and World Resources Institute. https://openknowledge.worldbank.org/handle/10986/31430.

Bruijnzeel, L.A., M. Mulligan, and F.N. Scatena. 2011. “Hydrometeorology of Tropical Montane Cloud Forests: Emerging Patterns.” Hydrological Processes 25 (3): 465–98. https://doi.org/10.1002/hyp.7974.

Bruijnzeel, L.A., and J. Proctor. 1995. “Hydrology and Biogeochemistry of Tropical Montane Cloud Forests: What Do We Really Know?” In Tropical Montane Cloud Forests, edited by L.S. Hamilton, J.O. Juvik, and F.N. Scatena. Vol. 110. New York: Springer.

Buchanan, A.H., and S.B. Levine. 1999. “Wood-Based Building Materials and Atmospheric Carbon Emissions.” Environmental Science & Policy 2 (6): 427–37. https://doi.org/10.1016/S1462-9011(99)00038-6.

Buchholz, T., M.D. Hurteau, J. Gunn, and D. Saah. 2016. “A Global Meta-analysis of Forest Bioenergy Greenhouse Gas Emission Accounting Studies.” GCB Bioenergy 8 (2): 281–89. https://doi.org/10.1111/gcbb.12245.

Buckingham, K., S. Ray, B. Arakwiye, A.G. Morales, R. Singh, O. Maneerattana, S. Wicaksono, H. Chrysolite, A. Minnick, and L. Johnston. 2018. Mapping Social Landscapes: A Guide to Identifying the Networks, Priorities, and Values of Restoration Actors. Washington, DC: World Resources Institute. https://files.wri.org/d8/s3fs-public/18_Guide_SocialMapping_FINAL3.pdf.

Burnett, R., H. Chen, M. Szyszkowicz, N. Fann, B. Hubbell, C.A. Pope, J.S. Apte, et al. 2018. “Global Estimates of Mortality Associated with Long-Term Exposure to Outdoor Fine Particulate Matter.” Proceedings of the National Academy of Sciences of the United States of America 115 (38): 9592–97. https://doi.org/10.1073/pnas.1803222115.

Busch, J., J. Engelmann, S.C. Cook-Patton, B.W. Griscom, T. Kroeger, H. Possingham, and P. Shyamsundar. 2019. “Potential for Low-Cost Carbon Dioxide Removal through Tropical Reforestation.” Nature Climate Change 9 (June): 463–66. https://doi.org/10.1038/s41558-019-0485-x.

Cai, M., Z. Xin, and X. Yu. 2017. “Spatio-temporal Variations in PM Leaf Deposition: A Meta-analysis.” Environmental Pollution 231, Part 1 (December): 207–18. https://doi.org/10.1016/j.envpol.2017.07.105.

Calder, I.R. 2007. “Forests and Water—Ensuring Forest Benefits Outweigh Water Costs.” Forest Ecology and Management 251 (1–2): 110–20. https://doi.org/10.1016/j.foreco.2007.06.015.

Calfapietra, C., S. Fares, F. Manes, A. Morani, G. Sgrigna, and F. Loreto. 2013. “Role of Biogenic Volatile Organic Compounds (BVOC) Emitted by Urban Trees on Ozone Concentration in Cities: A Review.” Environmental Pollution 183 (December): 71–80. https://doi.org/10.1016/j.envpol.2013.03.012.

California Urban Forest Council. 2018. “Urban Forest Management Plan Toolkit.” https://ufmptoolkit.net/.

Calogiuri, G., and S. Chroni. 2014. “The Impact of the Natural Environment on the Promotion of Active Living: An Integrative Systematic Review.” BMC Public Health 14 (August). https://doi.org/10.1186/1471-2458-14-873.

Cameron, R.W.F., and T. Blanuša. 2016. “Green Infrastructure and Ecosystem Services: Is the Devil in the Detail?” Annals of Botany 118 (3): 377–91. https://doi.org/10.1093/aob/mcw129.

Cardinale, B.J., J.E. Duffy, A. Gonzalez, D.U. Hooper, C. Perrings, P. Venail, A. Narwani, et al. 2012. “Biodiversity Loss and Its Impact on Humanity.” Nature 486 (June): 59–67. https://doi.org/10.1038/nature11148.

Cariñanos, P., P. Calaza-Martínez, L. O’Brien, and C. Calfapietra. 2017. “The Cost of Greening: Disservices of Urban Trees.” In The Urban Forest, edited by D. Pearlmutter, C. Calfapietra, R. Samson, L. O’Brien, S. Krajter Ostoić, G. Sanesi, and R. Alonso del Amo, 79–87. Cham: Springer International. https://doi.org/10.1007/978-3-319-50280-9_9.

Cariñanos, P., and M. Casares-Porcel. 2011. “Urban Green Zones and Related Pollen Allergy: A Review. Some Guidelines for Designing Spaces with Low Allergy Impact.” Landscape and Urban Planning 101 (3): 205–14. https://doi.org/10.1016/j.landurbplan.2011.03.006.

Carmichael, C.E., and M.H. McDonough. 2018. “The Trouble with Trees? Social and Political Dynamics of Street Tree-Planting Efforts in Detroit, Michigan, USA.” Urban Forestry & Urban Greening 31 (April): 221–29. https://doi.org/10.1016/j.ufug.2018.03.009.

Carvalho-Santos, C., J.P. Honrado, and L. Hein. 2014. “Hydrological Services and the Role of Forests: Conceptualization and Indicator-Based Analysis with an Illustration at a Regional Scale.” Ecological Complexity 20 (December): 69–80. https://doi.org/10.1016/j.ecocom.2014.09.001.

Cavanagh, J.-A.E., and J. Clemons. 2006. “Do Urban Forests Enhance Air Quality?” Australasian Journal of Environmental Management 13 (2): 120–30. https://doi.org/10.1080/14486563.2006.10648678.

Cavanaugh, K.C., J.S. Gosnell, S.L. Davis, J. Ahumada, P. Boundja, D.B. Clark, B. Mugerwa, et al. 2014. “Carbon Storage in Tropical Forests Correlates with Taxonomic Diversity and Functional Dominance on a Global Scale: Biodiversity and Aboveground Carbon Storage.” Global Ecology and Biogeography 23 (5): 563–73. https://doi.org/10.1111/geb.12143.

Cazzolla Gatti, R., J. Liang, A. Velichevskaya, and M. Zhou. 2019. “Sustainable Palm Oil May Not Be So Sustainable.” Science of the Total Environment 652 (February): 48–51. https://doi.org/10.1016/j.scitotenv.2018.10.222.

CBD (Convention on Biological Diversity) Secretariat. 2007. “Message from Mr. Ahmed Djoghlaf, Executive Secretary, on the Occasion of the International Day for Biological Diversity.” Montreal: United Nations Environment Programme. https://www.cbd.int/doc/speech/2007/sp-2007-05-22-es-en.pdf.

CBD Secretariat. 2014. Cities and Biodiversity Outlook: Action and Policy—a Global Assessment of the Links between Urbanization, Biodiversity, and Ecosystem Services. Montreal: CBD Secretariat. https://www.cbd.int/doc/health/cbo-action-policy-en.pdf.

CBD Secretariat. n.d. “Country Profiles: Indonesia—Main Details.” https://www.cbd.int/countries/profile/?country=id.

CBO (Congressional Budget Office). 2015. Public Spending on Transportation and Water Infrastructure, 1956 to 2014. Washington, DC: CBO. https://www.cbo.gov/sites/default/files/114th-congress-2015-2016/reports/49910-infrastructure.pdf.

Ceballos, G., P.R. Ehrlich, A.D. Barnosky, A. García, R.M. Pringle, and T.M. Palmer. 2015. "Accelerated Modern Human-Induced Species Losses: Entering the Sixth Mass Extinction.” Science Advances 1 (5): e1400253. https://doi.org/10.1126/sciadv.1400253.

Ceballos, G., P.R. Ehrlich, and R. Dirzo. 2017. “Biological Annihilation via the Ongoing Sixth Mass Extinction Signaled by Vertebrate Population Losses and Declines.” Proceedings of the National Academy of Sciences of the United States of America 114 (30): E6089–96. https://doi.org/10.1073/pnas.1704949114.

Central Arkansas Water. n.d. “Supporting Our Communities.” https://carkw.com/about/supporting-our-communities/. Accessed September 7, 2020.

Cespedes-Payret, C., G. Pineiro, M. Achkar, O. Gutierrez, and D. Panario. 2009. “The Irruption of New Agro-industrial Technologies in Uruguay and Their Environmental Impacts on Soil, Water Supply and Biodiversity: A Review.” International Journal of Environment and Health 3 (2): 175. https://doi.org/10.1504/IJENVH.2009.024877.

Chace, J.F., and J.J. Walsh. 2006. “Urban Effects on Native Avifauna: A Review.” Landscape and Urban Planning 74 (1): 46–69. https://doi.org/10.1016/j.landurbplan.2004.08.007.

Chazdon, R.L., P.H.S. Brancalion, L. Laestadius, A. Bennett-Curry, K. Buckingham, C. Kumar, J. Moll-Rocek, I.C.G. Vieira, and S.J. Wilson. 2016. “When Is a Forest a Forest? Forest Concepts and Definitions in the Era of Forest and Landscape Restoration.” Ambio 45 (September): 538–50. https://doi.org/10.1007/s13280-016-0772-y.

Chazdon, R.L., E.N. Broadbent, D.M.A. Rozendaal, F. Bongers, A.M.A. Zambrano, T.M. Aide, P. Balvanera, et al. 2016. “Carbon Sequestration Potential of Second-Growth Forest Regeneration in the Latin American Tropics.” Science Advances 2 (5): e1501639. https://doi.org/10.1126/sciadv.1501639.

Chen, W.Y. 2015. “The Role of Urban Green Infrastructure in Offsetting Carbon Emissions in 35 Major Chinese Cities: A Nationwide Estimate.” Cities 44 (April): 112–20. https://doi.org/10.1016/j.cities.2015.01.005

Chester Zoo. 2019. “Chester Named World’s First Sustainable Palm Oil City.” https://www.chesterzoo.org/news/chester-named-worlds-first-sustainable-palm-oil-city-2/.

Chivian, E., and A. Bernstein. 2010. How Our Health Depends on Biodiversity. Boston: Center for Health and the Global Environment, Harvard Medical School. https://www.bu.edu/sph/files/2012/12/Chivian_and_Bernstein_2010_How_our_Health_Depends_on_Biodiversity.pdf.

Churkina, G., R. Grote, T.M. Butler, and M. Lawrence. 2015. “Natural Selection? Picking the Right Trees for Urban Greening.” Environmental Science & Policy 47 (March): 12–17. https://doi.org/10.1016/j.envsci.2014.10.014.

Churkina, G., A. Organschi, C.P.O. Reyer, A. Ruff, K. Vinke, Z. Liu, B.K. Reck, T.E. Graedel, and H.J. Schellnhuber. 2020. “Buildings as a Global Carbon Sink.” Nature Sustainability 3 (April): 269–76. https://doi.org/10.1038/s41893-019-0462-4.

Cilliers, S., J. Cilliers, R. Lubbe, and S. Siebert. 2013. “Ecosystem Services of Urban Green Spaces in African Countries—Perspectives and Challenges.” Urban Ecosystems 16 (4): 681–702. https://doi.org/10.1007/s11252-012-0254-3.

Cities4Forests. n.d.a. “About Cities4Forests.” https://www.wri.org/our-work/project/cities4forests/about-cities4forests. Accessed June 13, 2022.

Cities4Forests. n.d.b. “Forest Footprint.” https://forestfootprint.org/. Accessed June 13, 2022.

Cities4Forests. n.d.c. “Partner Forest Program.” https://www.partnerforests.org/. Accessed June 13, 2022.

City of Madison. n.d. “Urban Forestry Special Charge.” https://www.cityofmadison.com/streets/forestry/UrbanForestrySpecialCharge.cfm. Accessed June 13, 2022.

City of Melbourne. 2014. Urban Forest Strategy: Making a Great City Greener 2012–2032. Melbourne: City of Melbourne. https://www.melbourne.vic.gov.au/SiteCollectionDocuments/urban-forest-strategy.pdf.

City of Melbourne. 2017. Nature in the City Strategy: Thriving Biodiversity and Healthy Ecosystems. Melbourne: City of Melbourne. https://www.melbourne.vic.gov.au/SiteCollectionDocuments/nature-in-the-city-strategy.pdf.

City of Melbourne. 2019. Exceptional Tree Register. Melbourne: City of Melbourne. http://www.melbourne.vic.gov.au/community/greening-the-city/tree-protection-management/Pages/exceptional-tree-register.aspx.

City of Vancouver. 2012. Greenest City 2020 Action Plan. Vancouver: City of Vancouver. https://vancouver.ca/files/cov/Greenest-city-action-plan.pdf.

City Parks Alliance. n.d. “Portland’s Green Street Program.” https://cityparksalliance.org/resource/portland-green-street-program/.

Civitello, D.J., J. Cohen, H. Fatima, N.T. Halstead, J. Liriano, T.A. McMahon, C.N. Ortega, et al. 2015. “Biodiversity Inhibits Parasites: Broad Evidence for the Dilution Effect.” Proceedings of the National Academy of Sciences of the United States of America 112 (28): 8667–71. https://doi.org/10.1073/pnas.1506279112.

Clinton, N., M. Stuhlmacher, A. Miles, N.U. Aragon, M. Wagner, M. Georgescu, C. Herwig, and P. Gong. 2018. “A Global Geospatial Ecosystem Services Estimate of Urban Agriculture.” Earth’s Future 6 (1): 40–60. https://doi.org/10.1002/2017EF000536.

CNCA (Carbon Neutral Cities Alliance). n.d. “CNCA Innovation Fund.” https://carbonneutralcities.org/initiatives/innovation-fund/. Accessed June 15, 2022.

Cohen, S., D. Janicki-Deverts, and G.E. Miller. 2007. “Psychological Stress and Disease.” JAMA 298 (14): 1685. https://doi.org/10.1001/jama.298.14.1685.

Coley, P.D., and T.A. Kursar. 2014. “On Tropical Forests and Their Pests.” Science 343 (6166): 35–36. https://doi.org/10.1126/science.1248110.

Concepción, E.D., M. Moretti, F. Altermatt, M.P. Nobis, and M.K. Obrist. 2015. “Impacts of Urbanisation on Biodiversity: The Role of Species Mobility, Degree of Specialisation and Spatial Scale.” Oikos 124 (12): 1571–82. https://onlinelibrary.wiley.com/doi/abs/10.1111/oik.02166.

Cook-Patton, S.C., S.M. Leavitt, D. Gibbs, N.L. Harris, K. Lister, K.J. Anderson-Teixeira, R.D. Briggs, et al. 2020. “Mapping Carbon Accumulation Potential from Global Natural Forest Regrowth.” Nature 585 (September): 545–50. https://doi.org/10.1038/s41586-020-2686-x.

Copsey, T., S. Dalimunthe, L. Hoijtink, and N. Stoll. 2013. Indonesia: How the People of Indonesia Live with Climate Change and What Communication Can Do. London: BBC Media Action. https://dataportal.bbcmediaaction.org/site/assets/uploads/2016/07/Indonesia-Report.pdf.

Cornwall, W. 2017. “Is Wood a Green Source of Energy? Scientists Are Divided.” Science, January 5. https://www.sciencemag.org/news/2017/01/wood-green-source-energy-scientists-are-divided.

Coutts, C., and M. Hahn. 2015. “Green Infrastructure, Ecosystem Services, and Human Health.” International Journal of Environmental Research and Public Health 12 (8): 9768–98. https://doi.org/10.3390/ijerph120809768.

Crawford, A. 2020. “Cliff Hanger: After Nearly Running Out of Water in 2018, the South African City of Cape Town Aims to Rid Its Watersheds of Thirsty Non-native Trees.” The Nature Conservancy, August 28. https://www.nature.org/en-us/magazine/magazine-articles/removing-trees-to-save-water-in-cape-town/.

CRED (Centre for Research on the Epidemiology of Disasters). 2015. The Human Cost of Weather Related Disasters 1995–2015. Brussels: CRED, School of Public Health, Université Catholique de Louvain; Geneva: United Nations Office for Disaster Risk Reduction. https://www.unisdr.org/files/46796_cop21weatherdisastersreport2015.pdf.

Creed, I.F., J.A. Jones, E. Archer, M. Claassen, D. Ellison, S.G. McNulty, M. van Noordwijk, et al. 2019. “Managing Forests for Both Downstream and Downwind Water.” Frontiers in Forests and Global Change 2 (October): 64. https://doi.org/10.3389/ffgc.2019.00064.

Cronemberger, C., and E. Viveiros de Castro. 2009. “The Contribution of Serra dos Órgãos National Park to Biodiversity Conservation." In Biodiversity and Land Use Systems in the Fragmented Mata Atlântica of Rio de Janeiro, edited by H. Gaese, J.C. Torrico Albino, J. Wesenberg, and S. Schlüter, 93–104. Göttingen, Germany: Cuvillier Verlag.

Crouzeilles, R., M.S. Ferreira, R.L. Chazdon, D.B. Lindenmayer, J.B.B. Sansevero, L. Monteiro, A. Iribarrem, A.E. Latawiec, and B.B.N. Strassburg. 2017. “Ecological Restoration Success Is Higher for Natural Regeneration than for Active Restoration in Tropical Forests.” Science Advances 3 (11): e1701345. https://doi.org/10.1126/sciadv.1701345.

Crush, J.S., and G.B. Frayne. 2011. “Urban Food Insecurity and the New International Food Security Agenda.” Development Southern Africa 28 (4): 527–44. https://doi.org/10.1080/0376835X.2011.605571.

CSU (Colorado State University). n.d. “Forests to Faucets.” https://cfri.colostate.edu/projects/forests-to-faucets/. Accessed June 13, 2022.

CTNC (Conservation Trust for North Carolina). n.d. “Upper Neuse Clean Water Initiative.” https://ctnc.org/projects/upper-neuse-clean-water-initiative/. Accessed December 12, 2020.

Cuni-Sanchez, A., M.J.P. Sullivan, P.J. Platts, S.L. Lewis, R. Marchant, G. Imani, W. Hubau, et al. 2021. “High Aboveground Carbon Stock of African Tropical Montane Forests.” Nature 596 (August): 536–42. https://doi.org/10.1038/s41586-021-03728-4.

Currie, W.S., and K.M. Bergen. 2008. “Temperate Forest.” In Encyclopedia of Ecology, 2nd ed., edited by B. Fath, 647–56. Amsterdam: Elsevier. https://doi.org/10.1016/B978-0-444-63768-0.00704-6.

Curtis, A.J., D. Helmig, C. Baroch, R. Daly, and S. Davis. 2014. “Biogenic Volatile Organic Compound Emissions from Nine Tree Species Used in an Urban Tree-Planting Program.” Atmospheric Environment 95 (October): 634–43. https://doi.org/10.1016/j.atmosenv.2014.06.035.

Curtis, L., W. Rea, P. Smith-Willis, E. Fenyves, and Y. Pan. 2006. “Adverse Health Effects of Outdoor Air Pollutants.” Environment International 32 (6): 815–30. https://doi.org/10.1016/j.envint.2006.03.012.

Curtis, P.G., C.M. Slay, N.L. Harris, A. Tyukavina, and M.C. Hansen. 2018. “Classifying Drivers of Global Forest Loss.” Science 361 (6407): 1108–11. https://doi.org/10.1126/science.aau3445.

Cusser, S., J.L. Neff, and S. Jha. 2016. “Natural Land Cover Drives Pollinator Abundance and Richness, Leading to Reductions in Pollen Limitation in Cotton Agroecosystems.” Agriculture, Ecosystems & Environment 226 (June): 33–42. https://doi.org/10.1016/j.agee.2016.04.020.

Dahl, R. 2013. “Cooling Concepts: Alternatives to Air Conditioning for a Warm World.” Environmental Health Perspectives 121 (1). https://doi.org/10.1289/ehp.121-a18.

Dalton, J. 2018. “No Such Thing as Sustainable Palm Oil: ‘Certified’ Can Destroy Even More Wildlife, Say Scientists.” The Independent, December 9. https://www.independent.co.uk/climate-change/news/palm-oil-sustainable-certified-plantations-orangutans-indonesia-southeast-asia-greenwashing-purdue-a8674681.html.

Daniel, T.C., A. Muhar, A. Arnberger, O. Aznar, J.W. Boyd, K.M.A. Chan, R. Costanza, et al. 2012. “Contributions of Cultural Services to the Ecosystem Services Agenda.” Proceedings of the National Academy of Sciences of the United States of America 109 (23): 8812–19. https://doi.org/10.1073/pnas.1114773109.

Davidson, E.A., A.C. de Araújo, P. Artaxo, J.K. Balch, I.F. Brown, M.M. C. Bustamante, M.T. Coe, et al. 2012. "The Amazon Basin in Transition." Nature 481 (January): 321–28. https://doi.org/10.1038/nature10717.

De Beenhouwer, M., R. Aerts, and O. Honnay. 2013. “A Global Meta-analysis of the Biodiversity and Ecosystem Service Benefits of Coffee and Cacao Agroforestry.” Agriculture, Ecosystems & Environment 175 (August): 1–7. https://doi.org/10.1016/j.agee.2013.05.003.

DEC (New York State Department of Environmental Conservation). n.d. “Herp Atlas Project.” https://www.dec.ny.gov/animals/7140.html. Accessed September 2, 2020.

Decina, S.M., A.G. Ponette-González, and J.E. Rindy. 2020. “Urban Tree Canopy Effects on Water Quality via Inputs to the Urban Ground Surface.” In Forest-Water Interactions, edited by D.F. Levia, D.E. Carlyle-Moses, S. Iida, B. Michalzik, K. Nanko, and A. Tischer, 433–57. Cham, Switzerland: Springer International. https://doi.org/10.1007/978-3-030-26086-6_18.

DeFries, R.S., T. Rudel, M. Uriarte, and M. Hansen. 2010. “Deforestation Driven by Urban Population Growth and Agricultural Trade in the Twenty-First Century.” Nature Geoscience 3 (March): 178–81. https://doi.org/10.1038/ngeo756.

den Braver, N. R., J. Lakerveld, F. Rutters, L.J. Schoonmade, J. Brug, and J.W.J. Beulens. 2018. “Built Environmental Characteristics and Diabetes: A Systematic Review and Meta-analysis.” BMC Medicine 16 (1): 12. https://doi.org/10.1186/s12916-017-0997-z.

De Risi, R., F. Jalayer, F. De Paola, I. Iervolino, M. Giugni, M.E. Topa, E. Mbuya, A. Kyessi, G. Manfredi, and P. Gasparini. 2013. “Flood Risk Assessment for Informal Settlements.” Natural Hazards 69 (1): 1003–32. https://doi.org/10.1007/s11069-013-0749-0.

DDOT (District Department of Transportation). n.d. “DDOT Trees: Permits and Laws.”

Washington, DC: DDOT, Government of the District of Columbia. https://ddot.dc.gov/sites/default/files/dc/sites/ddot/publication/attachments/DDOT%20Tree%20Permits%20%20Laws.pdf. Accessed September 2, 2020.

Díaz, S., A. Hector, and D. Wardle. 2009. “Biodiversity in Forest Carbon Sequestration Initiatives: Not Just a Side Benefit.” Current Opinion in Environmental Sustainability 1 (October): 55–60. https://doi.org/10.1016/j.cosust.2009.08.001.

Dirzo, R., H.S. Young, M. Galetti, G. Ceballos, N.J.B. Isaac, and B. Collen. 2014. “Defaunation in the Anthropocene.” Science 345 (6195): 401–6. https://doi.org/10.1126/science.1251817.

Dixon, J., A.M. Omwega, S. Friel, C. Burns, K. Donati, and R. Carlisle. 2007. “The Health Equity Dimensions of Urban Food Systems.” Journal of Urban Health: Bulletin of the New York Academy of Medicine 84 (Suppl 1): 118–29. https://doi.org/10.1007/s11524-007-9176-4.

Dobbs, C., F.J. Escobedo, N. Clerici, F. de la Barrera, A.A. Eleuterio, I. MacGregor-Fors, S. Reyes-Paecke, A. Vásquez, J.D. Zea Camaño, and H.J. Hernández. 2019. "Urban Ecosystem Services in Latin America: Mismatch between Global Concepts and Regional Realities?” Urban Ecosystems 22 (February): 173–87. https://doi.org/10.1007/s11252-018-0805-3.

Dobbs, C., C.R. Nitschke, and D. Kendal. 2014. “Global Drivers and Tradeoffs of Three Urban Vegetation Ecosystem Services.” PLoS ONE 9 (11): e113000. https://doi.org/10.1371/journal.pone.0113000.

Don, A., J. Schumacher, and A. Freibauer. 2011. “Impact of Tropical Land-Use Change on Soil Organic Carbon Stocks—a Meta-analysis.” Global Change Biology 17 (4): 1658–70. https://doi.org/10.1111/j.1365-2486.2010.02336.x.

Donato, D.C., J.B. Kauffman, D. Murdiyarso, S. Kurnianto, M. Stidham, and M. Kanninen. 2011. “Mangroves among the Most Carbon-Rich Forests in the Tropics.” Nature Geoscience 4 (May): 293–97. https://doi.org/10.1038/ngeo1123.

Douglas, I. 2008. “Urban Hydrology.” In The Routledge Handbook of Urban Ecology, edited by I. Douglas, D. Goode, M. Houck, and R. Wang. London: Routledge. https://doi.org/10.4324/9780203839263.ch13.

Dreiseitl, H., J. Asbjørn, and B. Wanschura. 2015. Cost-Benefit Analysis of Bishan-Ang Mo Kio Park. Singapore: National University of Singapore. https://ramboll.com/-/media/files/rnewmarkets/herbert-dreiseitl_part-1_final-report_22052015.pdf?la=en.

Drummond, J. 1996. “Garden in the Machine: An Environmental History of Brazil’s Tijuca Forest.” Environmental History 1 (1): 83–105. https://doi.org/10.2307/3985065.

Ducatez, S., F. Sayol, D. Sol, and L. Lefebvre. 2018. “Are Urban Vertebrates City Specialists, Artificial Habitat Exploiters, or Environmental Generalists?” Integrative and Comparative Biology 58 (5): 929–38. https://doi.org/10.1093/icb/icy1012018.

Dudley, N., and S. Stolton. 2003. Running Pure: The Importance of Forest Protected Areas to Drinking Water. Washington, DC: World Bank/WWF Alliance for Forest Conservation and Sustainable Use. https://openknowledge.worldbank.org/handle/10986/15006.

Dwyer, J.F., H.W. Schroeder, and P.H. Gobster. 1991. “The Significance of Urban Trees and Forests: Toward a Deeper Understanding of Values.” Journal of Arboriculture 17 (10): 276–84. https://www.nrs.fs.usda.gov/pubs/jrnl/1991/nc_1991_dwyer_001.pdf.

Dye, C. 2008. “Health and Urban Living.” Science 319 (5864): 766–69. https://doi.org/10.1126/science.1150198.

Dzhambov, A.M., and D.D. Dimitrova. 2014. “Urban Green Spaces’ Effectiveness as a Psychological Buffer for the Negative Health Impact of Noise Pollution: A Systematic Review.” Noise & Health 16 (70): 157–65. https://doi.org/10.4103/1463-1741.134916.

Dzhambov, A.M., D.D. Dimitrova, and E.D. Dimitrakova. 2014. “Association between Residential Greenness and Birth Weight: Systematic Review and Meta-analysis.” Urban Forestry & Urban Greening 13 (4): 621–29. https://doi.org/10.1016/j.ufug.2014.09.004.

Eisenman, T.S., G. Churkina, S.P. Jariwala, P. Kumar, G.S. Lovasi, D.E. Pataki, K.R. Weinberger, and T.H. Whitlow. 2019. “Urban Trees, Air Quality, and Asthma: An Interdisciplinary Review.” Landscape and Urban Planning 187 (July): 47–59. https://doi.org/10.1016/j.landurbplan.2019.02.010.

Ellison, D. 2018. “Forests and Water.” Background Analytical Study 2. Prepared for the 13th Session of the United Nations Forum on Forests, New York, May 7–11. https://www.un.org/esa/forests/wp-content/uploads/2018/04/UNFF13_BkgdStudy_ForestsWater.pdf.

Ellison, D., M.N. Futter, and K. Bishop. 2012. “On the Forest Cover–Water Yield Debate: From Demand‐ to Supply‐Side Thinking.” Global Change Biology 18 (3): 806–20. https://doi.org/10.1111/j.1365-2486.2011.02589.x.

Ellison, D., C.E. Morris, B. Locatelli, D. Sheil, J. Cohen, D. Murdiyarso, V. Gutierrez, et al. 2017. “Trees, Forests and Water: Cool Insights for a Hot World.” Global Environmental Change 43 (March): 51–61. https://doi.org/10.1016/j.gloenvcha.2017.01.002.

Elmqvist, T., H. Setälä, S.N. Handel, S. Van Der Ploeg, J. Aronson, J.N. Blignaut, E. Gomez-Baggethun, D.J. Nowak, J. Kronenberg, and R. De Groot. 2015. “Benefits of Restoring Ecosystem Services in Urban Areas.” Current Opinion in Environmental Sustainability 14 (June): 101–8. https://doi.org/10.1016/j.cosust.2015.05.001.

Encyclopaedia Britannica. 2020. “The Boroughs of New York City.” https://www.britannica.com/place/New-York-City/The-boroughs.

Endreny, T., R. Santagata, A. Perna, C.D. Stefano, R.F. Rallo, and S. Ulgiati. 2017. “Implementing and Managing Urban Forests: A Much Needed Conservation Strategy to Increase Ecosystem Services and Urban Wellbeing.” In “Environmental Accounting Models and Nature Conservation Strategies,” edited by P.P. Franzese, G. Liu, and S. Aricò, special issue, Ecological Modelling 360 (September): 328–35. https://doi.org/10.1016/j.ecolmodel.2017.07.016.

EPA (U.S. Environmental Protection Agency). 2019. “Managing Air Quality: Control Strategies to Achieve Air Pollution Reduction.” August 28. https://www.epa.gov/air-quality-management-process/managing-air-quality-control-strategies-achieve-air-pollution.

Erwin, T.L. 1982. “Tropical Forests: Their Richness in Coleoptera and Other Arthropod Species.” The Coleopterists Bulletin 36 (1): 74–75. http://www.jstor.org/stable/4007977

Escobedo, F., S. Varela, M. Zhao, J.E. Wagner, and W. Zipperer. 2010. “Analyzing the Efficacy of Subtropical Urban Forests in Offsetting Carbon Emissions from Cities.” Environmental Science & Policy 13 (5): 362–72. https://doi.org/10.1016/j.envsci.2010.03.009.

Escobedo, F.J., N. Clerici, C.L. Staudhammer, A. Feged-Rivadeneira, J.C. Bohorquez, and G. Tovar. 2018. “Trees and Crime in Bogota, Colombia: Is the Link an Ecosystem Disservice or Service?” Land Use Policy 78 (November): 583–92. https://doi.org/10.1016/j.landusepol.2018.07.029.

Escobedo, F.J., T. Kroeger, and J.E. Wagner. 2011. “Urban Forests and Pollution Mitigation: Analyzing Ecosystem Services and Disservices.” Environmental Pollution 159 (8–9): 2078–87. https://doi.org/10.1016/j.envpol.2011.01.010.

Estoque, R.C., M. Ooba, V. Avitabile, Y. Hijioka, R. DasGupta, T. Togawa, and Y. Murayama. 2019. “The Future of Southeast Asia’s Forests.” Nature Communications 10 (April): 1829. https://doi.org/10.1038/s41467-019-09646-4.

Estrada, F., W.J.W. Botzen, and R.S.J. Tol. 2017. “A Global Economic Assessment of City Policies to Reduce Climate Change Impacts.” Nature Climate Change 7 (June): 403–6. https://doi.org/10.1038/nclimate3301.

Evans, G.W., S. Otto, and F.G. Kaiser. 2018. “Childhood Origins of Young Adult Environmental Behavior.” Psychological Science 29 (5): 679–87. https://doi.org/10.1177/0956797617741894.

Evans, T., S. Olson, J. Watson, K. Gruetzmacher, M. Pruvot, S. Jupiter, S. Wang, T. Clements, and K. Jung. 2020. Links between Ecological Integrity, Emerging Infectious Diseases Originating from Wildlife, and Other Aspects of Human Health: An Overview of the Literature. Bronx, NY: Wildlife Conservation Society. https://c532f75abb9c1c021b8c-e46e473f8aadb72cf2a8ea564b4e6a76.ssl.cf5.rackcdn.com/2020/05/22/8zqrkmzuna_Links_between_ecological_integrity_and_EIDs_originating_from_wildlife.pdf.

FAO (Food and Agriculture Organization of the United Nations). 2016. Global Forest Resources Assessment 2015: How Are the World’s Forests Changing? 2nd ed. Rome: FAO. http://www.fao.org/3/a-i4793e.pdf.

FAO. 2018. The State of the World’s Forests 2018: Forests Pathways to Sustainable Development. Rome: FAO. http://www.fao.org/3/i9535en/i9535en.pdf.

FAO. 2020. Global Forest Resources Assessment 2020—Key Findings. Rome: FAO. https://doi.org/10.4060/ca8753en.

FAO and CIFOR (Center for International Forestry Research). 2005. “Forests and Floods: Drowning in Fiction or Thriving on Facts?” Forest Perspectives 2. Bangkok: FAO; Bogor Barat: CIFOR. http://www.fao.org/3/ae929e/ae929e00.htm.

FAO, International Tropical Timber Organization, and United Nations Economic Commission for Europe. 2020. Forest Product Conversion Factors. Rome: FAO. https://www.itto.int/direct/topics/topics_pdf_download/topics_id=6402&no=1&disp=inline.

FAO and UNEP (United Nations Environment Programme). 2020a. “Forest Species and Genetic Diversity.” Chapter 3 of The State of the World’s Forests 2020: Forests, Biodiversity and People. Rome: FAO; Nairobi: UNEP. http://www.fao.org/3/ca8642en/online/ca8642en.html#chapter-3_1.

FAO and UNEP. 2020b. The State of the World’s Forests 2020: Forests, Biodiversity and People. Rome: FAO; Nairobi: UNEP. https://doi.org/10.4060/ca8642en.

Fares, S., E. Paoletti, C. Calfapietra, T.N. Mikkelsen, R. Samson, and D. Le Thiec. 2017. “Carbon Sequestration by Urban Trees.” In The Urban Forest, vol. 7, edited by D. Pearlmutter, C. Calfapietra, R. Samson, L. O’Brien, S. Krajter Ostoić, G. Sanesi, and R. Alonso del Amo, 31–39. Cham, Switzerland: Springer International. https://doi.org/10.1007/978-3-319-50280-9_4.

Farley, K.A., E.G. Jobbágy, and R.B. Jackson. 2005. “Effects of Afforestation on Water Yield: A Global Synthesis with Implications for Policy.” Global Change Biology 11 (10): 1565–76. https://doi.org/10.1111/j.1365-2486.2005.01011.x.

Farnsworth, N.R., and R.W. Morris. 1976. “Higher Plants: The Sleeping Giant of Drug Development.” American Journal of Pharmacy and the Sciences Supporting Public Health 148 (2): 46–52.

Fath, B., ed. 2018. Encyclopedia of Ecology. 2nd ed. Amsterdam: Elsevier.

Fatin, L. 2020. “Little Rock Green Bond Brings Forest Protection to the Fore in Preserving Water Supply.” Climate Bonds Initiative, October 15. https://www.climatebonds.net/2020/10/central-arkansas-water-bond-first-kind-us-green-munis-gray-green-water-infrastructure.

Favero, A., A. Daigneault, and B. Sohngen. 2020. “Forests: Carbon Sequestration, Biomass Energy, or Both?” Science Advances 6 (13). https://www.science.org/doi/10.1126/sciadv.aay6792.

Federici, S., D. Lee, and M. Herold. 2018. “Forest Mitigation: A Permanent Contribution to the Paris Agreement?” Working Paper. San Francisco: Climate and Land Use Alliance. http://www.climateandlandusealliance.org/wp-content/uploads/2018/12/Forest-Mitigation-a-Permanent-Contribution-to-the-Paris-Agreement-1.pdf.

Feltran-Barbieri, R., S. Ozment, P. Hamel, E. Gray, H.L. Mansur, T. Piazzetta Valente, J. Baladelli Ribeiro, and M.M. Matsumoto. 2018. Infraestrutura Natural para Água No Sistema Guandu, Rio de Janeiro. 72. São Paulo: World Resources Institute Brasil. https://wribrasil.org.br/pt/publicacoes/infraestrutura-natural-para-agua-no-sistema-guandu-rio-de-janeiro

Fetene, A., and H. Worku. 2013. “Planning for the Conservation and Sustainable Use of Urban Forestry in Addis Ababa, Ethiopia.” Urban Forestry & Urban Greening 12 (3): 367–79. https://doi.org/10.1016/j.ufug.2013.03.004.

Filoso, S., M.O. Bezerra, K.C.B. Weiss, and M.A. Palmer. 2017. “Impacts of Forest Restoration on Water Yield: A Systematic Review.” PLoS ONE 12 (8): e0183210. https://doi.org/10.1371/journal.pone.0183210.

Finlayson, R. 2013. “Indonesia Prepares to Expand Schemes That Pay for Environmental Services.” Agroforestry World (blog), March 15. https://blog.worldagroforestry.org/index.php/2013/03/15/indonesia-prepares-to-expand-schemes-that-pay-for-environmental-services/.

Fischer, J., D.B. Lindenmayer, and A.D. Manning. 2006. “Biodiversity, Ecosystem Function, and Resilience: Ten Guiding Principles for Commodity Production Landscapes.” Frontiers in Ecology and the Environment 4 (2): 80–86. https://doi.org/10.1890/1540-9295(2006)004[0080:BEFART]2.0.CO;2.

Fitzgerald, K. n.d. “Mountain Gorilla Tourism Drives Economic Growth and Conservation.” African Wildlife Foundation. https://www.awf.org/blog/mountain-gorilla-tourism-drives-economic-growth-and-conservation. Accessed June 13, 2022.

Flies, E.J., S. Mavoa, G.R. Zosky, E. Mantzioris, C. Williams, R. Eri, B.W. Brook, and J.C. Buettel. 2019. “Urban-Associated Diseases: Candidate Diseases, Environmental Risk Factors, and a Path Forward.” Environment International 133, Part A (December): 105187. https://doi.org/10.1016/j.envint.2019.105187.

Flörke, M., C. Schneider, and R.I. McDonald. 2018. “Water Competition between Cities and Agriculture Driven by Climate Change and Urban Growth.” Nature Sustainability 1 (January): 51–58. https://www.nature.com/articles/s41893-017-0006-8.

Flynn, D.F.B., N. Mirotchnick, M. Jain, M.I. Palmer, and S. Naeem. 2011. “Functional and Phylogenetic Diversity as Predictors of Biodiversity–Ecosystem-Function Relationships.” Ecology 92 (8): 1573–81. https://doi.org/10.1890/10-1245.1.

Folke, C., S. Carpenter, B. Walker, M. Scheffer, T. Elmqvist, L. Gunderson, and C.S. Holling. 2004. “Regime Shifts, Resilience, and Biodiversity in Ecosystem Management.” Annual Review of Ecology, Evolution, and Systematics 35 (1): 557–81. https://doi.org/10.1146/annurev.ecolsys.35.021103.105711.

Fondos de Agua. n.d. “The Water Funds.” https://www.fondosdeagua.org/en/the-water-funds/. Accessed June 14, 2022.

Fowler, D., U. Skiba, E. Nemitz, F. Choubedar, D. Branford, R. Donovan, and P. Rowland. 2004. “Measuring Aerosol and Heavy Metal Deposition on Urban Woodland and Grass Using Inventories of 210 Pb and Metal Concentrations in Soil.” Water, Air and Soil Pollution: Focus 4 (June): 483–99. https://doi.org/10.1023/B:WAFO.0000028373.02470.ba.

Freitas, S.R., C.L. Neves, and P. Chernicharo. 2006. “Tijuca National Park: Two Pioneering Restorationist Initiatives in Atlantic Forest in Southeastern Brazil.” Brazilian Journal of Biology 66 (4): 975–82. https://doi.org/10.1590/S1519-69842006000600004.

Frick, W.F., T. Kingston, and J. Flanders. 2020. “A Review of the Major Threats and Challenges to Global Bat Conservation.” Annals of the New York Academy of Sciences 1469 (1): 5–25. https://doi.org/10.1111/nyas.14045.

Frumkin, H. 2002. “Urban Sprawl and Public Health.” Public Health Reports 117 (May–June): 201–17. https://doi.org/10.1093/phr/117.3.201.

Fuller, R.A., K.N. Irvine, P. Devine-Wright, P.H. Warren, and K.J. Gaston. 2007. “Psychological Benefits of Greenspace Increase with Biodiversity.” Biology Letters 3 (4). https://doi.org/10.1098/rsbl.2007.0149.

Gaertner, M., J.R.U. Wilson, M.W. Cadotte, J.S. MacIvor, R.D. Zenni, and D.M. Richardson. 2017. “Non-native Species in Urban Environments: Patterns, Processes, Impacts and Challenges.” Biological Invasions 19 (December): 3461–69. https://doi.org/10.1007/s10530-017-1598-7.

Gallai, N., J.-M. Salles, J. Settele, and B.E. Vaissière. 2009. "Economic Valuation of the Vulnerability of World Agriculture Confronted with Pollinator Decline." Ecological Economics 68 (3): 810–21. https://doi.org/10.1016/j.ecolecon.2008.06.014.

Gascon, M., M. Triguero-Mas, D. Martinez, P. Dadvand, D. Rojas-Rueda, A. Plasencia, and M.J. Nieuwenhuijsen. 2016. “Residential Green Spaces and Mortality: A Systematic Review.” Environment International 86 (January): 60–67. https://doi.org/10.1016/j.envint.2015.10.013.

Gebrehiwot, S.G., D. Ellison, W. Bewket,Y. Seleshi, B.-I. Inogwabini, and K. Bishop. 2019. “The Nile Basin Waters and the West African Rainforest: Rethinking the Boundaries.” Wiley Interdisciplinary Reviews Water 6 (1): e1317. https://doi.org/10.1002/wat2.1317.

Gerrish, E., and S.L. Watkins. 2018. “The Relationship between Urban Forests and Income: A Meta-analysis.” Landscape and Urban Planning 170 (February): 293–308. https://doi.org/10.1016/j.landurbplan.2017.09.005.

Gibbons, K.H., and C.M. Ryan. 2015. “Characterizing Comprehensiveness of Urban Forest Management Plans in Washington State.” Urban Forestry & Urban Greening 14 (3): 615–24. https://doi.org/10.1016/j.ufug.2015.06.003.

Gibbs, D., N. Harris, and J.R. Pool. 2022. Global Protocol for Community-Scale Greenhouse Gas Inventories: Supplemental Guidance for Forests and Trees. Washington, DC: Greenhouse Gas Protocol, World Resources Institute. https://ghgprotocol.org/gpc-supplemental-guidance-forests-and-trees.

Gibbs, D., N. Harris, and F. Seymour. 2018. “By the Numbers: The Value of Tropical Forests in the Climate Change Equation.” Insights (blog), October 4. https://www.wri.org/insights/numbers-value-tropical-forests-climate-change-equation#:~:text=If%20tropical%20deforestation%20were%20a,year%20between%202015%20and%202017.

GIO (Green Infrastructure Ontario Coalition). 2015. Ontario’s Urban Forests: Call to Action. Ontario: GIO. https://greeninfrastructureontario.org/app/uploads/2016/06/GIO_Urban_Forest_Call_to_Action_Sept15Print.pdf.

GIO. n.d. Communicating the Benefits of the Urban Forest in a Municipal Context: Toolkit Part 1. Ontario: GIO. https://greeninfrastructureontario.org/app/uploads/2016/06/UF-Toolkit-Part-I-Communicating-Benefits-Bulletin-Final.pdf. Accessed February 3, 2021.

Goh, X.P., M. Radhakrishnan, C. Zevenbergen, and A. Pathirana. 2017. “Effectiveness of Runoff Control Legislation and Active, Beautiful, Clean (ABC) Waters Design Features in Singapore.” Water 9 (8): 627. https://doi.org/10.3390/w9080627.

Goldstein, A., W.R. Turner, S.A. Spawn, K.J. Anderson-Teixeira, S. Cook-Patton, J. Fargione, H.K. Gibbs, et al. 2020. “Protecting Irrecoverable Carbon in Earth’s Ecosystems.” Nature Climate Change 10 (April): 287–95. https://doi.org/10.1038/s41558-020-0738-8.

González, E., M.R. Felipe-Lucia, B. Bourgeois, B. Boz, C. Nilsson, G. Palmer, and A.A. Sher. 2017. "Integrative Conservation of Riparian Zones." Biological Conservation 211, Part B (July): 20–29. https://doi.org/10.1016/j.biocon.2016.10.035.

Graham, D.A., J.K. Vanos, N.A. Kenny, and R.D. Brown. 2016. “The Relationship between Neighbourhood Tree Canopy Cover and Heat-Related Ambulance Calls during Extreme Heat Events in Toronto, Canada.” Urban Forestry & Urban Greening 20 (December): 180–86. https://doi.org/10.1016/j.ufug.2016.08.005.

Gray, E., S. Ozment, J. Carlos Altamirano, R. Feltran-Barbieri, and G. Morales. 2019. “Green-Gray Assessment: How to Assess the Costs and Benefits of Green Infrastructure for Water Supply Systems” Working Paper. Washington, DC: World Resources Institute. https://www.wri.org/publication/green-gray-assessment.

Green, J. 2013. “The New Philadelphia Story Is about Green Infrastructure.” The Dirt: Uniting the Built and Natural Environments, December 18. https://dirt.asla.org/2013/12/18/the-new-philadelphia-story-is-about-green-infrastructure/.Green>.Green City Partnerships. 2019. Best Management Practices for Crime Prevention through Environmental Design in Natural Landscapes. Seattle: Green City Partnerships, Forterra. https://www.greenseattle.org/wp-content/uploads/2019/02/CPTED-in-Natural-Areas-Final-Draft-Feb-2018_web.pdf.

Griscom, B.W., J. Adams, P.W. Ellis, R.A. Houghton, G. Lomax, D.A. Miteva, W.H. Schlesinger, et al. 2017. “Natural Climate Solutions.” Proceedings of the National Academy of Sciences of the United States of America 114 (44): 11645–50. https://doi.org/10.1073/pnas.1710465114.

Griscom, B.W., J. Busch, S.C. Cook-Patton, P.W. Ellis, J. Funk, S.M. Leavitt, G. Lomax, et al. 2020. “National Mitigation Potential from Natural Climate Solutions in the Tropics.” Philosophical Transactions of the Royal Society B: Biological Sciences 375 (1794): 20190126. https://doi.org/10.1098/rstb.2019.0126.

Grossman, E. 2013. “Declining Bee Populations Pose a Threat to Global Agriculture.” Yale Environment 360, April 30. https://e360.yale.edu/features/declining_bee_populations_pose_a_threat_to_global_agriculture.

Guégan, J.-F., A. Ayouba, J. Cappelle, and B. de Thoisy. 2020. “Forests and Emerging Infectious Diseases: Unleashing the Beast Within.” Environmental Research Letters 15 (8): 083007. https://doi.org/10.1088/1748-9326/ab8dd7.

Guerra, C.A., R.W. Snow, and S.I. Hay. 2006. “A Global Assessment of Closed Forests, Deforestation and Malaria Risk.” Annals of Tropical Medicine and Parasitology 100 (3): 189–204. https://doi.org/10.1179/136485906X91512.

Gunawardena, K.R., M.J. Wells, and T. Kershaw. 2017. “Utilising Green and Bluespace to Mitigate Urban Heat Island Intensity.” Science of the Total Environment 584–585 (April): 1040–55. https://doi.org/10.1016/j.scitotenv.2017.01.158.

Gunnell, K., M. Mulligan, R.A. Francis, and D.G. Hole. 2019. “Evaluating Natural Infrastructure for Flood Management within the Watersheds of Selected Global Cities.” Science of The Total Environment 670 (June): 411–24. https://doi.org/10.1016/j.scitotenv.2019.03.212.

Gustavsson, L., K. Pingoud, and R. Sathre. 2006. “Carbon Dioxide Balance of Wood Substitution: Comparing Concrete- and Wood-Framed Buildings.” Mitigation and Adaptation Strategies for Global Change 11 (3): 667–91. https://doi.org/10.1007/s11027-006-7207-1.

Guswa, A.M., D. Tetzlaff, J.S. Selker, D.E. Carlyle-Moses, E.W. Boyer, M. Bruen, C. Cayuela, et al. 2020. “Advancing Ecohydrology in the 21st Century: A Convergence of Opportunities.” Ecohydrology 13 (4): e2208. https://doi.org/10.1002/eco.2208.

Guyot, V., B. Castagneyrol, A. Vialatte, M. Deconchat, and H. Jactel. 2016. “Tree Diversity Reduces Pest Damage in Mature Forests across Europe.” Biology Letters 12 (4): 20151037. https://doi.org/10.1098/rsbl.2015.1037.

Haase, D., N. Larondelle, E. Andersson, M. Artmann, S. Borgström, J. Breuste, E. Gomez-Baggethun, et al. 2014. “A Quantitative Review of Urban Ecosystem Service Assessments: Concepts, Models, and Implementation.” Ambio 43 (May): 413–433. https://doi.org/10.1007/s13280-014-0504-0.

Hallegatte, S., C. Green, R.J. Nicholls, and J. Corfee-Morlot. 2013. “Future Flood Losses in Major Coastal Cities.” Nature Climate Change 3 (September): 802–6. https://doi.org/10.1038/nclimate1979.

Hamilton, S.E., and D. Casey. 2016. “Creation of a High Spatio-temporal Resolution Global Database of Continuous Mangrove Forest Cover for the 21st Century (CGMFC-21): CGMFC-21.” Global Ecology and Biogeography 25 (6): 729–38. https://doi.org/10.1111/geb.12449.

Hankey, S., and J.D. Marshall. 2017. “Urban Form, Air Pollution, and Health.” Current Environmental Health Reports 4 (December): 491–503. https://doi.org/10.1007/s40572-017-0167-7.

Hansen, M.C., P.V. Potapov, R. Moore, M. Hancher, S.A. Turubanova, A. Tyukavina, D. Thau, et al. 2013. “High-Resolution Global Maps of 21st-Century Forest Cover Change.” Science 342 (6160): 850–53. https://doi.org/10.1126/science.1244693.

Hansen, M.M., R. Jones, and K. Tocchini. 2017. “Shinrin-Yoku (Forest Bathing) and Nature Therapy: A State-of-the-Art Review.” International Journal of Environmental Research and Public Health 14 (8). https://doi.org/10.3390/ijerph14080851.

Hanson, C., and J. Ranganathan. 2022. “How to Manage the Global Land Squeeze? Produce, Protect, Reduce, Restore.” Insights (blog), February 14. https://www.wri.org/insights/manage-global-land-squeeze-produce-protect-reduce-restore.

Harlan, S.L., A.J. Brazel, L. Prashad, W.L. Stefanov, and L. Larsen. 2006. “Neighborhood Microclimates and Vulnerability to Heat Stress.” Social Science & Medicine 63 (11): 2847–63. https://doi.org/10.1016/j.socscimed.2006.07.030.

Harris, N., T. Munroe, E. Goldman, C. Slay, and F. Follett. 2020. “Agriculture Drove Recent Record-Breaking Tree Cover Loss.” Insights (blog), February 21. https://www.wri.org/insights/agriculture-drove-recent-record-breaking-tree-cover-loss.

Harris, N.L., D.A. Gibbs, A. Baccini, R.A. Birdsey, S. de Bruin, M. Farina, L. Fatoyinbo, et al. 2021. “Global Maps of Twenty-First Century Forest Carbon Fluxes.” Nature Climate Change 11 (March): 234–40. https://doi.org/10.1038/s41558-020-00976-6.

Harte, A.M. 2017. “Mass Timber: The Emergence of a Modern Construction Material.” Journal of Structural Integrity and Maintenance 2 (3): 121–32. https://doi.org/10.1080/24705314.2017.1354156.

Hartig, T., R. Mitchell, S. de Vries, and H. Frumkin. 2014. “Nature and Health.” Annual Review of Public Health 35 (March): 207–28. https://doi.org/10.1146/annurev-publhealth-032013-182443.

Harvard Health Publishing. 2014. “Peptic Ulcer.” December 29. https://www.health.harvard.edu/digestive-health/peptic-ulcer-overview.

Hausmann, A., R. Slotow, J.K. Burns, and E.D. Minin. 2016. “The Ecosystem Service of Sense of Place: Benefits for Human Well-Being and Biodiversity Conservation.” Environmental Conservation 43 (2): 117–27. https://doi.org/10.1017/S0376892915000314.

Heaviside, C., H. Macintyre, and S. Vardoulakis. 2017. “The Urban Heat Island: Implications for Health in a Changing Environment.” Current Environmental Health Reports 4 (September): 296–305. https://doi.org/10.1007/s40572-017-0150-3.

Henders, S., U.M. Persson, and T. Kastner. 2015. “Trading Forests: Land-Use Change and Carbon Emissions Embodied in Production and Exports of Forest-Risk Commodities.” Environmental Research Letters 10 (12): 125012. https://doi.org/10.1088/1748-9326/10/12/125012.

Hess, D.E. 2019. “Philadelphia Green City, Clean Waters Green Infrastructure Program Saves $50 Million/Year, Generated $4 Billion In Economic Impact So Far.” PA Environment Digest Blog, April 16. http://paenvironmentdaily.blogspot.com/2019/04/philadelphia-green-city-clean-waters.html.Hewitt,/a>.Hewitt, C.N., K. Ashworth, and A.R. MacKenzie. 2020. “Using Green Infrastructure to Improve Urban Air Quality (GI4AQ).” Ambio 49 (January): 62–73. https://doi.org/10.1007/s13280-019-01164-3.

Heynen, N., H.A. Perkins, and P. Roy. 2006. “The Political Ecology of Uneven Urban Green Space: The Impact of Political Economy on Race and Ethnicity in Producing Environmental Inequality in Milwaukee.” Urban Affairs Review 42 (1): 3–25. https://doi.org/10.1177/1078087406290729.

Higgs, E. 2003. Nature by Design: People, Natural Process, and Ecological Restoration. Cambridge, MA: MIT Press. https://mitpress.mit.edu/books/nature-design.

Hill, S.L.L., A. Arnell, C. Maney, S.H.M. Butchart, C. Hilton-Taylor, C. Ciciarelli, C. Davis, E. Dinerstein, A. Purvis, and N.D. Burgess. 2019. “Measuring Forest Biodiversity Status and Changes Globally.” Frontiers in Forests and Global Change 29 (November). https://doi.org/10.3389/ffgc.2019.00070.

Hipólito, J., B. dos Santos Bandiera Sousa, R.C. Borges, R.M. de Brito, R. Jaffé, S. Dias, V.L. Imperatriz Fonseca, and T.C. Giannini. 2019. "Valuing Nature's Contribution to People: The Pollination Services Provided by Two Protected Areas in Brazil." Global Ecology and Conservation 20 (October): e00782. https://doi.org/10.1016/j.gecco.2019.e00782.

Hisano, M., E.B. Searle, and H.Y.H. Chen. 2018. “Biodiversity as a Solution to Mitigate Climate Change Impacts on the Functioning of Forest Ecosystems.” Biological Reviews 93 (1): 439–56. https://doi.org/10.1111/brv.12351.

Hofste, R.W., P. Reig, and L. Schleifer. 2019. “17 Countries, Home to One-Quarter of the World’s Population, Face Extremely High Water Stress.” Insights (blog), August 6. https://www.wri.org/insights/17-countries-home-one-quarter-worlds-population-face-extremely-high-water-stress.

Holl, K.D., and P.H.S. Brancalion. 2020. “Tree Planting Is Not a Simple Solution.” Science 368 (6491): 580–81. https://doi.org/10.1126/science.aba8232.

Holling, C.S. 1973. “Resilience and Stability of Ecological Systems.” Annual Review of Ecology and Systematics 4 (November): 1–23. https://doi.org/10.1146/annurev.es.04.110173.000245.

Hosonuma, N., M. Herold, V. De Sy, R.S. De Fries, M. Brockhaus, L. Verchot, A. Angelsen, and E. Romijn. 2012. “An Assessment of Deforestation and Forest Degradation Drivers in Developing Countries.” Environmental Research Letters 7 (4): 044009. https://doi.org/10.1088/1748-9326/7/4/044009.

Hua, F., X. Wang, X. Zheng, B. Fisher, L. Wang, J. Zhu, Y. Tang, D.W. Yu, and D.S. Wilcove. 2016. “Opportunities for Biodiversity Gains under the World’s Largest Reforestation Programme.” Nature Communications 7 (September): 12717. https://doi.org/10.1038/ncomms12717.

Huang, Y., Y. Chen, N. Castro-Izaguirre, M. Baruffol, M. Brezzi, A. Lang, Y. Li, et al. 2018. “Impacts of Species Richness on Productivity in a Large-Scale Subtropical Forest Experiment.” Science 362 (6410): 80–83. https://doi.org/10.1126/science.aat6405.

Hubau, W., S.L. Lewis, O.L. Phillips, K. Affum-Baffoe, H. Beeckman, A. Cuní-Sanchez, A.K. Daniels, et al. 2020. "Asynchronous Carbon Sink Saturation in African and Amazonian Tropical Forests." Nature 579 (7797): 80–87. https://doi.org/10.1038/s41586-020-2035-0.

Hubbard, R.M., J. Stape, M.G. Ryan, A.C. Almeida, and J. Rojas. 2010. “Effects of Irrigation on Water Use and Water Use Efficiency in Two Fast Growing Eucalyptus Plantations.” Forest Ecology and Management 259 (9): 1714–21. https://doi.org/10.1016/j.foreco.2009.10.028.

Hylander, K., and S. Nemomissa. 2009. “Complementary Roles of Home Gardens and Exotic Tree Plantations as Alternative Habitats for Plants of the Ethiopian Montane Rainforest.” Conservation Biology 23 (2): 400–409. https://doi.org/10.1111/j.1523-1739.2008.01097.x.

Ideno, Y., K. Hayashi, Y. Abe, K. Ueda, H. Iso, M. Noda, J.-S. Lee, and S. Suzuki. 2017. “Blood Pressure–Lowering Effect of Shinrin-Yoku (Forest Bathing): A Systematic Review and Meta-analysis.” BMC Complementary and Alternative Medicine 17 (August): 409. https://doi.org/10.1186/s12906-017-1912-z.

IEA (International Energy Agency). 2018. The Future of Cooling: Opportunities for Energy-Efficient Air Conditioning. Paris: Organisation for Economic Co-operation and Development and IEA. https://iea.blob.core.windows.net/assets/0bb45525-277f-4c9c-8d0c-9c0cb5e7d525/The_Future_of_Cooling.pdf.

IEA and UNEP (United Nations Environment Programme). 2018. 2018 Global Status Report towards a Zero-Emission, Efficient and Resilient Buildings and Construction Sector. Prepared for the Global Alliance for Buildings and Construction. Nairobi: UNEP. https://www.worldgbc.org/sites/default/files/2018%20GlobalABC%20Global%20Status%20Report.pdf.

Ilstedt, U., A. Malmer, E. Verbeeten, and D. Murdiyarso. 2007. “The Effect of Afforestation on Water Infiltration in the Tropics: A Systematic Review and Meta-analysis.” Forest Ecology and Management 251 (1–2): 45–51. https://doi.org/10.1016/j.foreco.2007.06.014.

Intasen, M., R.J. Hauer, L.P. Werner, and E. Larsen. 2016. “Urban Forest Assessment in Bangkok, Thailand.” Journal of Sustainable Forestry 36 (2): 148–63. https://doi.org/10.1080/10549811.2016.1265455.

IPBES (Intergovernmental Science-Policy Platform on Biodiversity and Ecosystem Services). 2016. The Assessment Report of the Intergovernmental Science-Policy Platform on Biodiversity and Ecosystem Services on Pollinators, Pollination and Food Production: Summary for Policymakers. Edited by S.G. Potts, V.L. Imperatriz-Fonseca, H.T. Ngo, J.C. Biesmeijer, T.D. Breeze, L.V. Dicks, L.A. Garibaldi, et al. Bonn, Germany: IPBES Secretariat. https://ipbes.net/assessment-reports/pollinators.

IPBES. 2019. Global Assessment Report on Biodiversity and Ecosystem Services. Edited by E.S. Brondizio, J. Settele, S. Díaz, and H.T. Ngo. Bonn, Germany: IPBES Secretariat. https://doi.org/10.5281/zenodo.3831673.

IPBES. n.d. “About: What Is IPBES?” https://ipbes.net/about#:~:text=The%20Intergovernmental%20Science%2DPolicy%20Platform,%2C%20long%2Dterm%20human%20well%2D. Accessed February 14, 2021.

IPCC (Intergovernmental Panel on Climate Change). 2018. Global Warming of 1.5°C. An IPCC Special Report on the Impacts of Global Warming of 1.5°C above Pre-industrial Levels and Related Global Greenhouse Gas Emission Pathways, in the Context of Strengthening the Global Response to the Threat of Climate Change, Sustainable Development, and Efforts to Eradicate Poverty, edited by V. Masson-Delmotte, P. Zhai, H.-O. Pörtner, D. Roberts, J. Skea, P.R. Shukla, A. Pirani, et al. Cambridge and New York: Cambridge University Press. https://doi.org/10.1017/9781009157940.

IPCC. 2019. Climate Change and Land: An IPCC Special Report on Climate Change, Desertification, Land Degradation, Sustainable Land Management, Food Security, and Greenhouse Gas Fluxes in Terrestrial Ecosystems. Edited by P.R. Shukla, J. Skea, E. Calvo Buendia, V. Masson-Delmotte, H.-O. Pörtner, D.C. Roberts, P. Zhai, et al. Cambridge and New York: Cambridge University Press. https://www.ipcc.ch/site/assets/uploads/2019/11/SRCCL-Full-Report-Compiled-191128.pdf.

Irvine, K.N., and S. Herrett. 2018. “Does Ecosystem Quality Matter for Cultural Ecosystem Services?” Journal for Nature Conservation 46 (December): 1–5. https://doi.org/10.1016/j.jnc.2018.08.010.

Isbell, F., V. Calcagno, A. Hector, J. Connolly, W.S. Harpole, P.B. Reich, M. Scherer-Lorenzen, et al. 2011. “High Plant Diversity Is Needed to Maintain Ecosystem Services.” Nature 477 (September): 199–202. https://doi.org/10.1038/nature10282.

Ishii, H.T., T. Manabe, K. Ito, N. Fujita, A. Imanishi, D. Hashimoto, and A. Iwasaki. 2010. “Integrating Ecological and Cultural Values toward Conservation and Utilization of Shrine/Temple Forests as Urban Green Space in Japanese Cities.” Landscape and Ecological Engineering 6 (July): 307–15. https://doi.org/10.1007/s11355-010-0104-5.

Islam, R., and G. Walkerden. 2014. “How Bonding and Bridging Networks Contribute to Disaster Resilience and Recovery on the Bangladeshi Coast.” International Journal of Disaster Risk Reduction 10, Part A (December): 281–91. https://doi.org/10.1016/j.ijdrr.2014.09.016.

IUCN. n.d. “Our Work: Nature-based Solutions.” https://www.iucn.org/theme/nature-based-solutions. Accessed February 17, 2021.

Jacob, D.J., and D.A. Winner. 2009. “Effect of Climate Change on Air Quality.” Atmospheric Environment 43 (1): 51–63. https://doi.org/10.1016/j.atmosenv.2008.09.051.

Jactel, H., E.S. Gritti, L. Drössler, D.I. Forrester, W.L. Mason, X. Morin, H. Pretzsch, and B. Castagneyrol. 2018. "Positive Biodiversity—Productivity Relationships in Forests: Climate Matters." Biology Letters 14 (4): 20170747. https://doi.org/10.1098/rsbl.2017.0747.

Jaenicke, J., S. Englhart, and F. Siegert. 2011. “Monitoring the Effect of Restoration Measures in Indonesian Peatlands by Radar Satellite Imagery.” Journal of Environmental Management 92 (3): 630–38. https://doi.org/10.1016/j.jenvman.2010.09.029.

Janhäll, S. 2015. "Review on Urban Vegetation and Particle Air Pollution—Deposition and Dispersion.” Atmospheric Environment 105: 130–37. https://doi.org/10.1016/j.atmosenv.2015.01.052.

Jansson, M., H. Fors, T. Lindgren, and B. Wistrom. 2013. “Perceived Personal Safety in Relation to Urban Woodland Vegetation: A Review.” Urban Forestry & Urban Greening 12 (2): 127–33. https://doi.org/10.1016/j.ufug.2013.01.005.

Jelks, N.O., V. Jennings, and A. Rigolon. 2021. “Green Gentrification and Health: A Scoping Review.” International Journal of Environmental Research and Public Health 18 (3): 907. https://doi.org/10.3390/ijerph18030907.

Jenkins, C.N., S.L. Pimm, and L.N. Joppa. 2013. “Global Patterns of Terrestrial Vertebrate Diversity and Conservation.” Proceedings of the National Academy of Sciences of the United States of America 110 (28): E2602–10. https://doi.org/10.1073/pnas.1302251110.

Jennings, V., and O. Bamkole. 2019. “The Relationship between Social Cohesion and Urban Green Space: An Avenue for Health Promotion.” International Journal of Environmental Research and Public Health 16 (3): 452. https://doi.org/10.3390/ijerph16030452.

Jennings, V., A.K. Baptiste, N. Osborne Jelks, and R. Skeete. 2017. “Urban Green Space and the Pursuit of Health Equity in Parts of the United States.” International Journal of Environmental Research and Public Health 14 (11): 1432. https://doi.org/10.3390/ijerph14111432.

Jennings, V., and C. Johnson Gaither. 2015. “Approaching Environmental Health Disparities and Green Spaces: An Ecosystem Services Perspective.” International Journal of Environmental Research and Public Health 12 (2): 1952–68. https://doi.org/10.3390/ijerph120201952.

Jennings, V., C. Johnson Gaither, and R. Schulterbrandt Gragg. 2012. “Promoting Environmental Justice through Urban Green Space Access: A Synopsis.” Environmental Justice 5 (1): 1–7. https://doi.org/10.1089/env.2011.0007.

Jennings, V., L. Larson, and J. Yun. 2016. “Advancing Sustainability through Urban Green Space: Cultural Ecosystem Services, Equity, and Social Determinants of Health.” International Journal of Environmental Research and Public Health 13 (2): 196. https://doi.org/10.3390/ijerph13020196.

Jha, A.K., R. Bloch, and J. Lamond. 2012. Cities and Flooding: A Guide to Integrated Urban Flood Risk Management for the 21st Century. Washington, DC: World Bank. https://doi.org/10.1596/978-0-8213-8866-2.

Jia, G., E. Shevliakova, P. Artaxo, N. De Noblet-Ducoudré, R. Houghton, J. House, K. Kitajima, et al. 2019. “Land–Climate Interactions.” In Climate Change and Land: An IPCC Special Report on Climate Change, Desertification, Land Degradation, Sustainable Land Management, Food Security, and Greenhouse Gas Fluxes in Terrestrial Ecosystems, edited by P.R. Shukla, J. Skea, E. Calvo Buendia, V. Masson-Delmotte, H.-O. Pörtner, D. C. Roberts, P. Zhai, et al., 131–248. Cambridge and New York: Cambridge University Press.

Jianan, X., O. Zhiyun, Z. Hua, W. Xiaoke, and M. Hong. 2007. “Allergenic Pollen Plants and Their Influential Factors in Urban Areas.” Acta Ecologica Sinica 27 (9): 3820–27. https://doi.org/10.1016/S1872-2032(07)60082-1.

Jim, C.Y. 2005. “Monitoring the Performance and Decline of Heritage Trees in Urban Hong Kong.” Journal of Environmental Management 74 (2): 161–72. https://doi.org/10.1016/j.jenvman.2004.08.014.

Jim, C.Y., and W.Y. Chen. 2009. “Ecosystem Services and Valuation of Urban Forests in China.” Cities 26 (4): 187–94. https://doi.org/10.1016/j.cities.2009.03.003.

Jo, H.-K., H.-M. Park, and J.-Y. Kim. 2019. “Carbon Offset Service and Design Guideline of Tree Planting for Multifamily Residential Sites in Korea.” Sustainability 11 (13): 3543. https://doi.org/10.3390/su11133543.

Johnson, E., and D. Smith. 2006. Legacy: Conserving New York State’s Biodiversity. Albany: American Museum of Natural History, New York State Biodiversity Research Institute, New York State Department of Environmental Conservation, New York Natural Heritage Program, and The Nature Conservancy. https://www.natureserve.org/biodiversity-science/publications/legacy-conserving-new-york-states-biodiversity.

Jones, B.A., D. Grace, R. Kock, S. Alonso, J. Rushton, M.Y. Said, D. McKeever, et al. 2013. “Zoonosis Emergence Linked to Agricultural Intensification and Environmental Change.” Proceedings of the National Academy of Sciences of the United States of America 110 (21): 8399–8404. https://doi.org/10.1073/pnas.1208059110.

Jones, J.A., X. Wei, E. Archer, K. Bishop, J.A. Blanco, D. Ellison, M.B. Gush, S.G. McNulty, M. van Noordwijk, and I.F. Creed. 2020. “Forest-Water Interactions under Global Change.” In Forest-Water Interactions, edited by D.F. Levia, D.E. Carlyle-Moses, S. Iida, B. Michalzik, K. Nanko, and A. Tischer, 589–624. Cham, Switzerland: Springer International. https://doi.org/10.1007/978-3-030-26086-6_24.

Jong, H.N. 2019. “Europe, in Bid to Phase Out Palm Biofuel, Leaves Fans and Foes Dismayed.” Mongabay, March 15. https://news.mongabay.com/2019/03/europe-in-bid-to-phase-out-palm-biofuel-leaves-fans-and-foes-dismayed/.

Juno, E., and S. Hines. 2019. “Lumber Salvaged from Baltimore’s Row Houses and City Trees Creates Jobs and Cuts Wood Waste.” Insights (blog), October 4. https://www.wri.org/insights/lumber-salvaged-baltimores-row-houses-and-city-trees-creates-jobs-and-cuts-wood-waste.

Juno, E., and J.R. Pool. 2020. “How Forests Near or Far Can Protect Water for Cities.” Insights (blog), September 23. https://www.wri.org/insights/forests-near-or-far-can-protect-water-cities.

Juno, E., and T. Virsilas. 2019. “Urban Forests for Healthier Cities: Policy, Planning, Regulations, and Institutional Arrangements: Learning Guide.” Cities4Forests. https://cities4forests.com/lg-urban-forests-for-healthier-cities/.

Kamitsis, I., and A.J.P. Francis. 2013. “Spirituality Mediates the Relationship between Engagement with Nature and Psychological Wellbeing.” Journal of Environmental Psychology 36 (December): 136–43. https://doi.org/10.1016/j.jenvp.2013.07.013.

Kapos, V., S. Wicander, T. Salvaterra, K. Dawkins, and C. Hicks. 2019. “The Role of the Natural Environment in Adaptation.” Background Paper. Rotterdam and Washington, DC: Global Commission on Adaptation. https://gca.org/wp-content/uploads/2020/12/RoleofNaturalEnvironmentinAdaptation_V2.pdf.

Karesh, W.B., A. Dobson, J.O. Lloyd-Smith, J. Lubroth, M.A. Dixon, M. Bennett, S. Aldrich, et al. 2012. “Ecology of Zoonoses: Natural and Unnatural Histories.” Lancet 380 (9857): 1936–45. https://doi.org/10.1016/S0140-6736(12)61678-X.

Karjalainen, E., T. Sarjala, and H. Raitio. 2010. “Promoting Human Health through Forests: Overview and Major Challenges.” Environmental Health and Preventive Medicine 15 (1): 1–8. https://doi.org/10.1007/s12199-008-0069-2.

Kearns, C.A., D.W. Inouye, and N.M. Waser. 1998. “Endangered Mutualisms: The Conservation of Plant-Pollinator Interactions.” Annual Review of Ecology and Systematics 29 (1): 83–112. https://doi.org/10.1146/annurev.ecolsys.29.1.83.

Keenan, R.J., G.A. Reams, F. Achard, J.V. de Freitas, A. Grainger, and E. Lindquist. 2015. “Dynamics of Global Forest Area: Results from the FAO Global Forest Resources Assessment 2015.” Forest Ecology and Management 352 (September): 9–20. https://doi.org/10.1016/j.foreco.2015.06.014.

Khan, F., and C. Borgstrom-Hansson. 2016. “Using the Earth Hour City Challenge to Identify High Leverage Points for Footprint Reduction in Cities.” Journal of Cleaner Production, Advancing Sustainable Solutions: An Interdisciplinary and Collaborative Research Agenda 123 (June): 42–44. https://doi.org/10.1016/j.jclepro.2015.06.128.

Kier, G., H. Kreft, T.M. Lee, W. Jetz, P.L. Ibisch, C. Nowicki, J. Mutke, and W. Barthlott. 2009. “A Global Assessment of Endemism and Species Richness across Island and Mainland Regions.” Proceedings of the National Academy of Sciences of the United States of America 106 (23): 9322–27. https://doi.org/10.1073/pnas.0810306106.

King County. 2020. “Forest Carbon Program.” March 17. https://kingcounty.gov/services/environment/water-and-land/forestry/forest-carbon.aspx.

Klein, A.-M., B.E. Vaissière, J.H. Cane, I. Steffan-Dewenter, S.A. Cunningham, C. Kremen, and T. Tscharntke. 2007. "Importance of Pollinators in Changing Landscapes for World Crops." Proceedings of the Royal Society B: Biological Sciences 274 (1608): 303–13. https://doi.org/10.1098/rspb.2006.3721.

Kloog, I. 2019. “Air Pollution, Ambient Temperature, Green Space and Preterm Birth.” Current Opinion in Pediatrics 31 (2): 237–43. https://doi.org/10.1097/MOP.0000000000000736.

Ko, Y. 2018. “Trees and Vegetation for Residential Energy Conservation: A Critical Review for Evidence-Based Urban Greening in North America.” Urban Forestry & Urban Greening 34 (August): 318–35. https://doi.org/10.1016/j.ufug.2018.07.021.

Kohl, H.W., C.L. Craig, E.V. Lambert, S. Inoue, J.R. Alkandari, G. Leetongin, and S. Kahlmeier. 2012. “The Pandemic of Physical Inactivity: Global Action for Public Health.” Lancet 380 (9838): 294–305. https://doi.org/10.1016/S0140-6736(12)60898-8.

Kolbert, E. 2014. The Sixth Extinction: An Unnatural History. New York: Henry Holt.

Kondo, M.C., J.M. Fluehr, T. McKeon, and C.C. Branas. 2018. “Urban Green Space and Its Impact on Human Health.” International Journal of Environmental Research and Public Health 15 (3): 445. https://doi.org/10.3390/ijerph15030445.

Kondo, M.C., S. Han, G.H. Donovan, and J.M. MacDonald. 2017. “The Association between Urban Trees and Crime: Evidence from the Spread of the Emerald Ash Borer in Cincinnati.” Landscape and Urban Planning 157 (January): 193–99. https://doi.org/10.1016/j.landurbplan.2016.07.003.

Kondo, M.C., N. Mueller, D.H. Locke, L.A. Roman, D. Rojas-Rueda, L.H. Schinasi, M. Gascon, and M.J. Nieuwenhuijsen. 2020. “Health Impact Assessment of Philadelphia’s 2025 Tree Canopy Cover Goals.” Lancet Planetary Health 4 (4): e149–57. https://doi.org/10.1016/S2542-5196(20)30058-9.

Kondo, M.C., E.C. South, and C.C. Branas. 2015. “Nature-Based Strategies for Improving Urban Health and Safety.” Journal of Urban Health: Bulletin of the New York Academy of Medicine 92 (5): 800–814. https://doi.org/10.1007/s11524-015-9983-y.

Kovats, R.S., and S. Hajat. 2008. “Heat Stress and Public Health: A Critical Review.” Annual Review of Public Health 29 (1): 41–55. https://doi.org/10.1146/annurev.publhealth.29.020907.090843.

Kremen, C., N.M. Williams, R.L. Bugg, J.P. Fay, and R.W. Thorp. 2004. “The Area Requirements of an Ecosystem Service: Crop Pollination by Native Bee Communities in California.” Ecology Letters 7 (11): 1109–19. https://doi.org/10.1111/j.1461-0248.2004.00662.x.

Krishnan, S., G. Wiederkehr Guerra, D. Bertrand, S. Wertz-Kanounnikoff, and C.J. Kettle. 2020. “The Pollination Services of Forests.” Forestry Working Paper 15. Rome: Food and Agriculture Organization of the United Nations and Bioversity International. https://doi.org/10.4060/ca9433en.

Kuddus, M.A., E. Tynan, and E. McBryde. 2020. “Urbanization: A Problem for the Rich and the Poor?” Public Health Review 41 (1). https://doi.org/10.1186/s40985-019-0116-0.

Kuehler, E., J. Hathaway, and A. Tirpak. 2017. “Quantifying the Benefits of Urban Forest Systems as a Component of the Green Infrastructure Stormwater Treatment Network.” Ecohydrology 10 (3): e1813. https://doi.org/10.1002/eco.1813.

Kumar, P., A. Druckman, J. Gallagher, B. Gatersleben, S. Allison, T.S. Eisenman, U. Hoang, et al. 2019. “The Nexus between Air Pollution, Green Infrastructure and Human Health.” Environment International 133, Part A (December): 105181. https://doi.org/10.1016/j.envint.2019.105181.

Kuo, F.E. 2003. “Social Aspects of Urban Forestry: The Role of Arboriculture in a Healthy Social Ecology.” Journal of Arboriculture 29 (3): 148–55.

Kuo, M. 2015. “How Might Contact with Nature Promote Human Health? Promising Mechanisms and a Possible Central Pathway.” Frontiers in Psychology 6 (August). https://doi.org/10.3389/fpsyg.2015.01093.

Lachowycz, K., and A.P. Jones. 2011. “Greenspace and Obesity: A Systematic Review of the Evidence.” Obesity Reviews 12 (5): e183–89. https://doi.org/10.1111/j.1467-789X.2010.00827.x.

Lai, H., E.J. Flies, P. Weinstein, and A. Woodward. 2019. “The Impact of Green Space and Biodiversity on Health.” Frontiers in Ecology and the Environment 17 (7): 383–90. https://doi.org/10.1002/fee.2077.

Landrigan, P.J., R. Fuller, N.J.R. Acosta, O. Adeyi, R. Arnold, N. Basu, A.B. Baldé, et al. 2018. "The Lancet Commission on Pollution and Health.” Lancet Commissions 391 (10119): 462–512. https://www.thelancet.com/journals/lancet/article/PIIS0140-6736(17)32345-0/fulltext.

Laothawornkitkul, J., J.E. Taylor, N.D. Paul, and C.N. Hewitt. 2009. “Biogenic Volatile Organic Compounds in the Earth System.” New Phytologist 183 (1): 27–51. https://doi.org/10.1111/j.1469-8137.2009.02859.x.

Lara, A., C. Little, R. Urrutia, J. McPhee, C. Álvarez-Garretón, C. Oyarzún, D. Soto, et al. 2009. "Assessment of Ecosystem Services as an Opportunity for the Conservation and Management of Native Forests in Chile." In “Old Forests, New Management: the Conservation and Use of Old-Growth Forests in the 21st Century,” edited by C. Beadle, G. Duff, and A. Richardson, special issue, Forest Ecology and Management 258 (4): 415–24. https://doi.org/10.1016/j.foreco.2009.01.004.

Laurance, W.F. 2007. “Forests and Floods.” Nature 449 (September): 409–10. https://doi.org/10.1038/449409a.

Law, B.E., T.W. Hudiburg, L.T. Berner, J.J. Kent, P.C. Buotte, and M.E. Harmon. 2018. “Land Use Strategies to Mitigate Climate Change in Carbon Dense Temperate Forests.” Proceedings of the National Academy of Sciences of the United States of America 115 (14): 3663–68. https://doi.org/10.1073/pnas.1720064115.

Lawrence, D., and K. Vandecar. 2015. “Effects of Tropical Deforestation on Climate and Agriculture.” Nature Climate Change 5 (January): 27–36. https://doi.org/10.1038/nclimate2430.

Lecic-Tosevski, D. 2019. “Is Urban Living Good for Mental Health?” Current Opinion in Psychiatry 32 (3): 204–9. https://doi.org/10.1097/YCO.0000000000000489.

Lee, A.C.K., and R. Maheswaran. 2011. “The Health Benefits of Urban Green Spaces: A Review of the Evidence.” Journal of Public Health 33 (2): 212–22. https://doi.org/10.1093/pubmed/fdq068.

Lee, I., H. Choi, K.-S. Bang, S. Kim, M. Song, and B. Lee. 2017. “Effects of Forest Therapy on Depressive Symptoms among Adults: A Systematic Review.” International Journal of Environmental Research and Public Health 14 (3): 321. https://doi.org/10.3390/ijerph14030321.

Lele, S. 2009. “Watershed Services of Tropical Forests: From Hydrology to Economic Valuation to Integrated Analysis.” Current Opinion in Environmental Sustainability 1 (2): 148–55. https://doi.org/10.1016/j.cosust.2009.10.007.

Le Quéré, C., R.M. Andrew, P. Friedlingstein, S. Sitch, J. Pongratz, A.C. Manning, J.I. Korsbakken, et al. 2018. "Global Carbon Budget 2017." Earth System Science Data 10 (1): 405–48. https://doi.org/10.5194/essd-10-405-2018.

Leung, D.Y.C., J.K.Y. Tsui, F. Chen, Y. Wing-Kin, L.L.P. Vrijmoed, and L. Chun-Ho. 2011. “Effects of Urban Vegetation on Urban Air Quality.” Landscape Research 36 (2): 173–88. https://doi.org/10.1080/01426397.2010.547570.

Lewis, S.L., C.E. Wheeler, E.T.A. Mitchard, and A. Koch. 2019. “Restoring Natural Forests Is the Best Way to Remove Atmospheric Carbon.” Nature 568 (7750): 25–28. https://doi.org/10.1038/d41586-019-01026-8.

Li, Q. 2010. “Effect of Forest Bathing Trips on Human Immune Function.” Environmental Health and Preventive Medicine 15 (January): 9–17. https://doi.org/10.1007/s12199-008-0068-3.

Li, Q., K. Morimoto, M. Kobayashi, H. Inagaki, M. Katsumata, Y. Hirata, K. Hirata, et al. 2008. “Visiting a Forest, but Not a City, Increases Human Natural Killer Activity and Expression of Anti-cancer Proteins.” International Journal of Immunopathology and Pharmacology 21 (1): 117–27. https://doi.org/10.1177/039463200802100113.

Li, X., Y. Zhou, S. Yu, G. Jia, H. Li, and W. Li. 2019. “Urban Heat Island Impacts on Building Energy Consumption: A Review of Approaches and Findings.” Energy 174 (May): 407–19. https://doi.org/10.1016/j.energy.2019.02.183.

Liang, J., T.W. Crowther, N. Picard, S. Wiser, M. Zhou, G. Alberti, E.-D. Schulze, et al. 2016. “Positive Biodiversity-Productivity Relationship Predominant in Global Forests.” Science 354 (6309): aaf8957. https://doi.org/10.1126/science.aaf8957.

Lindley, S., S. Pauleit, K. Yeshitela, S. Cilliers, and C. Shackleton. 2018. “Rethinking Urban Green Infrastructure and Ecosystem Services from the Perspective of Sub-Saharan African Cities.” Landscape and Urban Planning 180 (December): 328–38. https://doi.org/10.1016/j.landurbplan.2018.08.016.

Litschke, T., and W. Kuttler. 2008. “On the Reduction of Urban Particle Concentration by Vegetation: A Review.” Meteorologische Zeitschrift 17 (3): 229–40. https://doi.org/10.1127/0941-2948/2008/0284.

Little, C., A. Lara, J. McPhee, and R. Urrutia. 2009. “Revealing the Impact of Forest Exotic Plantations on Water Yield in Large Scale Watersheds in South-Central Chile.” Journal of Hydrology 374 (1): 162–70. https://doi.org/10.1016/j.jhydrol.2009.06.011.

LoGiudice, K., R.S. Ostfeld, K.A. Schmidt, and F. Keesing. 2003. “The Ecology of Infectious Disease: Effects of Host Diversity and Community Composition on Lyme Disease Risk.” Proceedings of the National Academy of Sciences of the United States of America 100 (2): 567–71. https://doi.org/10.1073/pnas.0233733100.

Lõhmus, M., and J. Balbus. 2015. "Making Green Infrastructure Healthier Infrastructure." Infection Ecology & Epidemiology 5 (1): 30082. https://doi.org/10.3402/iee.v5.30082.

Louv, R. 2005. Last Child in the Woods: Saving Our Children from Nature Deficit Disorder. Chapel Hill, NC: Algonquin.

Lovejoy, T.E., and C. Nobre. 2018. “Amazon Tipping Point.” Science Advances 4 (2): eaat2340. https://doi.org/10.1126/sciadv.aat2340.

Lozano-Baez, S.E., M. Cooper, P. Meli, S.F.B. Ferraz, R.R. Rodrigues, and T.J. Sauer. 2019. “Land Restoration by Tree Planting in the Tropics and Subtropics Improves Soil Infiltration, but Some Critical Gaps Still Hinder Conclusive Results.” Forest Ecology and Management 444 (July): 89–95. https://doi.org/10.1016/j.foreco.2019.04.046.

Luber, G., and M. McGeehin. 2008. “Climate Change and Extreme Heat Events.” American Journal of Preventive Medicine 35 (5): 429–35. https://doi.org/10.1016/j.amepre.2008.08.021.

Lundgren, K., and T. Kjellstrom. 2013. “Sustainability Challenges from Climate Change and Air Conditioning Use in Urban Areas.” Sustainability 5 (7): 3116–28. https://doi.org/10.3390/su5073116.

Luntz, T. 2009. “City’s ‘All Green’ Stormwater Plan Raises Eyebrows at EPA.” New York Times, December 24. https://archive.nytimes.com/www.nytimes.com/gwire/2009/12/24/24greenwire-citys-all-green-stormwater-plan-raises-eyebrow-45258.html.

Luqman, M., T.M. Butt, A. Tanvir, M. Atiq, M.Z. Yousuf Hussan, and M. Yaseen. 2013. “Phytoremediation of Polluted Water by Tress: A Review.” African Journal of Agricultural Research 8 (17): 1591–95. https://doi.org/10.5897/AJAR11.1111.

Lwasa, S., F. Mugagga, B. Wahab, D. Simon, J.P. Connors, and C. Griffith. 2015. “A Meta-analysis of Urban and Peri-urban Agriculture and Forestry in Mediating Climate Change.” Current Opinion in Environmental Sustainability 13 (April): 68–73. https://doi.org/10.1016/j.cosust.2015.02.003.

Lyons-White, J., and A.T. Knight. 2018. “Palm Oil Supply Chain Complexity Impedes Implementation of Corporate No-Deforestation Commitments.” Global Environmental Change 50 (May): 303–13. https://doi.org/10.1016/j.gloenvcha.2018.04.012.

Lyytimäki, J., L.K. Petersen, B. Normander, and P. Bezák. 2008. "Nature as a Nuisance? Ecosystem Services and Disservices to Urban Lifestyle." Environmental Sciences 5 (3): 161–72. https://doi.org/10.1080/15693430802055524.

Lyytimäki, J., and M. Sipilä. 2009. "Hopping on One Leg: The Challenge of Ecosystem Disservices for Urban Green Management.” Urban Forestry & Urban Greening 8 (4): 309–15. https://doi.org/10.1016/j.ufug.2009.09.003.

Mahmood, R., R.A. Pielke, K.G. Hubbard, D. Niyogi, P.A. Dirmeyer, C. McAlpine, A.M. Carleton, et al. 2014. “Land Cover Changes and Their Biogeophysical Effects on Climate.” International Journal of Climatology 34 (4): 929–53. https://doi.org/10.1002/joc.3736.

Makarieva, A.M., and V.G. Gorshkov. 2010. “The Biotic Pump: Condensation, Atmospheric Dynamics and Climate.” International Journal of Water 5 (4): 365. https://doi.org/10.1504/IJW.2010.038729.

Mallapaty, S. 2020. “Animal Source of the Coronavirus Continues to Elude Scientists.” Nature, May 18. https://doi.org/10.1038/d41586-020-01449-8.

Mallet-Rodrigues, F., J.F. Pacheco, and R. Parrini. 2007. “Birds of the Serra dos Órgãos, State of Rio de Janeiro, Southeastern Brazil: A Review." Revista Brasileira de Ornitologia 15 (1): 5–35.

Mancus, G.C., and J. Campbell. 2018. “Integrative Review of the Intersection of Green Space and Neighborhood Violence.” Journal of Nursing Scholarship 50 (2): 117–25. https://doi.org/10.1111/jnu.12365.

Maps of World. 2017. “Tijuca Forest, Rio de Janeiro Travel Information.” May 10. https://www.mapsofworld.com/travel/destinations/brazil/tijuca-forest.

Mapulanga, A.M., and H. Naito. 2019. “Effect of Deforestation on Access to Clean Drinking Water.” Proceedings of the National Academy of Sciences of the United States of America 116 (17): 8249–54. https://doi.org/10.1073/pnas.1814970116.

Marritz, L. 2013. “How Do You Calculate Stormwater Credits for Trees? Part 1: Why Tree-Based Credits Are Hard to Quantify.” DeepRoot Blog, March 25. https://www.deeproot.com/blog/blog-entries/how-do-you-calculate-stormwater-credits-for-trees-part-1-why-tree-based-credits-are-hard-to-quantify/.

Marron, N., and D. Epron. 2019. “Are Mixed-Tree Plantations Including a Nitrogen-Fixing Species More Productive than Monocultures?” Forest Ecology and Management 441 (June): 242–52. https://doi.org/10.1016/j.foreco.2019.03.052.

Marselle, M.R., J. Stadler, H. Korn, K. Irvine, and A. Bonn, eds. 2019. Biodiversity and Health in the Face of Climate Change. Cham, Switzerland: Springer International. https://doi.org/10.1007/978-3-030-02318-8.

Martin, C. 2015. “A Re-examination of the Pollinator Crisis.” Current Biology 25 (19): R811–15. https://doi.org/10.1016/j.cub.2015.09.022.

Maruthaveeran, S., and C.C. Konijnendijk van den Bosch. 2014. “A Socio-ecological Exploration of Fear of Crime in Urban Green Spaces: A Systematic Review.” Urban Forestry & Urban Greening 13 (1): 1–18. https://doi.org/10.1016/j.ufug.2013.11.006.

Marzluff, J., R. Bowman, and R. Donnelly, eds. 2001. “Worldwide Urbanization and Its Effects on Birds.” In Avian Ecology and Conservation in an Urbanizing World. Boston: Springer. https://doi.org/10.1007/978-1-4615-1531-9.

Masood, I., Z. Majid, S. Sohail, A. Zia, and S. Raza. 2015. “The Deadly Heat Wave of Pakistan, June 2015.” International Journal of Occupational and Environmental Medicine 6 (4): 247–48. https://doi.org/10.15171/ijoem.2015.672.

Mavuso, N. 2016. “Designing for Safer Inner-City Parks in Johannesburg.” SaferSpaces (blog), April 18. https://www.saferspaces.org.za/blog/entry/designing-for-safer-inner-city-parks-in-johannesburg.

May, R.M. 2010. “Tropical Arthropod Species, More or Less?” Science 329 (5987): 41–42. https://doi.org/10.1126/science.1191058.

Mazor, T., C. Doropoulos, F. Schwarzmueller, D.W. Gladish, N. Kumaran, K. Merkel, M. Di Marco, and V. Gagic. 2018. “Global Mismatch of Policy and Research on Drivers of Biodiversity Loss.” Nature Ecology & Evolution 2 (July): 1071–74. https://doi.org/10.1038/s41559-018-0563-x.

Mburu, J., L.G. Hein, B. Gemmill, and L. Collette. 2006. Economic Valuation of Pollination Services: Review of Methods. Rome: Food and Agriculture Organization of the United Nations. http://www.fao.org/fileadmin/templates/agphome/documents/Biodiversity-pollination/econvaluepoll1.pdf.

McCormick, R. 2017. “Does Access to Green Space Impact the Mental Well-Being of Children: A Systematic Review.” Journal of Pediatric Nursing 37 (December): 3–7. https://doi.org/10.1016/j.pedn.2017.08.027.

McDonald, R., T. Kroger, T. Boucher, W. Longzhu, and R. Slame. 2016. Planting Healthy Air: A Global Analysis of the Role of Urban Trees in Addressing Particulate Matter Pollution and Extreme Heat. Arlington, VA: The Nature Conservancy. https://www.nature.org/content/dam/tnc/nature/en/documents/20160825_PHA_Report_Final.pdf.

McDonald, R.I., T. Kroeger, P. Zhang, and P. Hamel. 2020. “The Value of US Urban Tree Cover for Reducing Heat-Related Health Impacts and Electricity Consumption.” Ecosystems 23 (1): 137–50. https://doi.org/10.1007/s10021-019-00395-5.

McDonald, R.I., and D. Shemie. 2014. Urban Water Blueprint: Mapping Conservation Solutions to the Global Water Challenge. Washington, DC: The Nature Conservancy.

McDonald, R.I., K.F. Weber, J. Padowski, T. Boucher, and D. Shemie. 2016. “Estimating Watershed Degradation over the Last Century and Its Impact on Water-Treatment Costs for the World’s Large Cities.” Proceedings of the National Academy of Sciences of the United States of America 113 (32): 9117–22. https://doi.org/10.1073/pnas.1605354113.

McDonald’s. 2022. “Nature, Forests & Water.” https://corporate.mcdonalds.com/corpmcd/our-purpose-and-impact/our-planet/nature-forests-water.html.

McEwen, B.S. 2008. “Central Effects of Stress Hormones in Health and Disease: Understanding the Protective and Damaging Effects of Stress and Stress Mediators.” European Journal of Pharmacology 583 (2–3): 174–85. https://doi.org/10.1016/j.ejphar.2007.11.071.

McGriff, E.C. 1972. “The Effects of Urbanization on Water Quality.” Journal of Environmental Quality 1 (1): 86–88. https://doi.org/10.2134/jeq1972.00472425000100010020x.

McKinney, M.L. 2008. “Effects of Urbanization on Species Richness: A Review of Plants and Animals.” Urban Ecosystems 11 (June): 161–76. https://doi.org/10.1007/s11252-007-0045-4.

McPhearson, T., D. Maddox, B. Gunther, and D. Bragdon. 2013. “Local Assessment of New York City: Biodiversity, Green Space, and Ecosystem Services.” In Urbanization, Biodiversity and Ecosystem Services: Challenges and Opportunities: A Global Assessment, edited by T. Elmqvist, M. Fragkias, J. Goodness, B. Güneralp, P.J. Marcotullio, R.I. McDonald, S. Parnell, et al., 355–83. Dordrecht: Springer Netherlands.

McPherson, E.G., D. Nowak, and R.A. Rowntree. 1994. “Chicago’s Urban Forest Ecosystem: Results of the Chicago Urban Forest Climate Project.” Radnor, PA: Northeastern Research Station, U.S. Department of Agriculture, Forest Service. https://www.fs.usda.gov/treesearch/pubs/4285.

McPherson, E.G., Q. Xiao, N.S. van Doorn, J. de Goede, J. Bjorkman, A. Hollander, R.M. Boynton, J.F. Quinn, and J.H. Thorne. 2017. “The Structure, Function and Value of Urban Forests in California Communities.” Urban Forestry & Urban Greening 28 (December): 43–53. https://doi.org/10.1016/j.ufug.2017.09.013.

Medvigy, D., R.L. Walko, M.J. Otte, and R. Avissar. 2013. “Simulated Changes in Northwest U.S. Climate in Response to Amazon Deforestation.” Journal of Climate 26 (22): 9115–36. https://doi.org/10.1175/JCLI-D-12-00775.1.

Melo, M., A. Pinheiro, E. Torres, G. Piazza, and V. Kaufmann. 2021. “Analysis of Phreatic Levels in Riparian Forest and Pasture in an Agricultural Watershed, Santa Catarina, Brazil.” In Advances in Geoethics and Groundwater Management: Theory and Practice for a Sustainable Development edited by M. Abrunhosa, A. Chambel, S. Peppoloni, and H.I. Chaminé, 169–72. Cham, Switzerland: Springer. https://doi.org/10.1007/978-3-030-59320-9_36.

Menéndez, P., I.J. Losada, S. Torres-Ortega, S. Narayan, and M.W. Beck. 2020. "The Global Flood Protection Benefits of Mangroves." Scientific Reports 10 (March): 4404. https://doi.org/10.1038/s41598-020-61136-6.

Meyer, K., and R. Bürger-Arndt. 2014. “How Forests Foster Human Health: Present State of Research-Based Knowledge (in the Field of Forests and Human Health).” International Forestry Review 16 (4): 421–46. https://doi.org/10.1505/146554814813484103.

Milestone, S., and P. Kremer. 2019. “Encouraging Councils and Governments around the World to Adopt Timber-First Policies: A Systematic Literature Review.” Mass Timber Construction Journal 2 (March): 8–14. https://journalmtc.com/index.php/mtcj/article/view/18.

Miljø-Direktoratet (Norwegian Environment Agency). 2019. “Sales of Advanecd Biofuels Increased Last Year.” May 3. https://www.miljodirektoratet.no/aktuelt/nyheter/2019/mai-2019/salget-av-avansert-biodrivstoff-okte-i-fjor/.

Millennium Ecosystem Assessment. 2005. Ecosystems and Human Well-Being: Synthesis. Washington, DC: Island. http://www.millenniumassessment.org/documents/document.356.aspx.pdf.

Mittermeier, R.A., W.R. Turner, F.W. Larsen, T.M. Brooks, and C. Gascon. 2011. “Global Biodiversity Conservation: The Critical Role of Hotspots.” In Biodiversity Hotspots: Distribution and Protection of Conservation Priority Areas, edited by F.E. Zachos and J.C. Habel, 3–22. Berlin: Springer. https://doi.org/10.1007/978-3-642-20992-5_1.

MMSD (Milwaukee Metropolitan Sewerage District). 2020. “MMSD Accelerating Green Program to Reduce Overflows and Protect Lake Michigan.” January 27. https://www.mmsd.com/about-us/news/mmsd-community-based-green-infrastructure-program-2020.

Mohajerani, A., J. Bakaric, and T. Jeffrey-Bailey. 2017. “The Urban Heat Island Effect, Its Causes, and Mitigation, with Reference to the Thermal Properties of Asphalt Concrete.” Journal of Environmental Management 197 (July): 522–38. https://doi.org/10.1016/j.jenvman.2017.03.095.

Monasterolo, M., M.L. Musicante, G.R. Valladares, and A. Salvo. 2015. “Soybean Crops May Benefit from Forest Pollinators.” Agriculture, Ecosystems & Environment 202 (April): 217–22. https://doi.org/10.1016/j.agee.2015.01.012.

Monath, T.P., and P.F.C. Vasconcelos. 2015. “Yellow Fever.” Journal of Clinical Virology 64 (March): 160–73. https://doi.org/10.1016/j.jcv.2014.08.030.

Montgomery County Government. 2017. Montgomery County Tree Canopy Law 2017 Annual Report. Rockville, MD: Montgomery County Government. https://www.montgomerycountymd.gov/DEP/Resources/Files/ReportsandPublications/Trees%20%26%20Air/Trees/County%20Reports/2017-Annual-Report.pdf.

Moore, J.C. 2018. “Predicting Tipping Points in Complex Environmental Systems.” Proceedings of the National Academy of Sciences of the United States of America 115 (4): 635–36. https://doi.org/10.1073/pnas.1721206115.

Mora, C., D.P. Tittensor, S. Adl, A.G.B. Simpson, and B. Worm. 2011. “How Many Species Are There on Earth and in the Ocean?” PLoS Biology 9 (8): e1001127. https://doi.org/10.1371/journal.pbio.1001127.

Morakinyo, T.E., A.A. Balogun, and O.B. Adegun. 2013. “Comparing the Effect of Trees on Thermal Conditions of Two Typical Urban Buildings.” Urban Climate 3 (May): 76–93. https://doi.org/10.1016/j.uclim.2013.04.002.

Morandin, L.A., and M.L. Winston. 2006. “Pollinators Provide Economic Incentive to Preserve Natural Land in Agroecosystems.” Agriculture, Ecosystems & Environment 116 (3–4): 289–92. https://doi.org/10.1016/j.agee.2006.02.012.

Moussa, S., B. Kyereh, A. Tougiani, S. Kuyah, and M. Saadou. 2019. “West African Sahelian Cities As Source of Carbon Stocks: Evidence from Niger.” Sustainable Cities and Society 50 (October): 101653. https://doi.org/10.1016/j.scs.2019.101653.

Mullaney, J., T. Lucke, and S.J. Trueman. 2015. “A Review of Benefits and Challenges in Growing Street Trees in Paved Urban Environments.” Landscape and Urban Planning 134 (February): 157–66. https://doi.org/10.1016/j.landurbplan.2014.10.013.

Myers, N., R.A. Mittermeier, C.G. Mittermeier, G.A.B. da Fonseca, and J. Kent. 2000. “Biodiversity Hotspots for Conservation Priorities.” Nature 403 (February): 853–58. https://doi.org/10.1038/35002501.

Nabuurs, G.J., O. Masera, K. Andrasko, P. Benitez-Ponce, R. Boer, M. Dutschke, E. Elsiddig, J. Ford-Robertson, et al. 2007. “Forestry.” In Climate Change 2007: Mitigation. Contribution of Working Group III to the Fourth Assessment Report of the Intergovernmental Panel on Climate Change, edited by B. Metz, O.R. Davidson, P.R. Bosch, R. Dave, and L.A. Meyer, 540–84. Cambridge and New York: Cambridge University Press. https://www.ipcc.ch/site/assets/uploads/2018/02/ar4-wg3-chapter9-1.pdf.

Nargi, L. 2019. “The Miyawaki Method: A Better Way to Build Forests?” JSTOR Daily (blog), July 24. https://daily.jstor.org/the-miyawaki-method-a-better-way-to-build-forests/.

Natarajan, R. 2017. “Medellin.” Flickr. https://flic.kr/p/23eGTEr.

Natural Capital Project n.d. “InVEST.” Stanford University. https://naturalcapitalproject.stanford.edu/software/invest. Accessed October 7, 2021.

Neary, D.G., G.G. Ice, and C.R. Jackson. 2009. “Linkages between Forest Soils and Water Quality and Quantity.” Forest Ecology and Management 258 (10): 2269–81. https://doi.org/10.1016/j.foreco.2009.05.027.

Nero, B.F., D. Callo-Concha, and M. Denich. 2018. “Structure, Diversity, and Carbon Stocks of the Tree Community of Kumasi, Ghana.” Forests 9 (9): 519. https://doi.org/10.3390/f9090519.

Nesbitt, L., N. Hotte, S. Barron, J. Cowan, and S.R.J. Sheppard. 2017. “The Social and Economic Value of Cultural Ecosystem Services Provided by Urban Forests in North America: A Review and Suggestions for Future Research.” Urban Forestry & Urban Greening 25 (July): 103–11. https://doi.org/10.1016/j.ufug.2017.05.005.

Newman, D.J., and G.M. Cragg. 2012. “Natural Products as Sources of New Drugs over the 30 Years from 1981 to 2010.” Journal of Natural Products 73 (3): 311–35. https://doi.org/https://doi.org/10.1021/np200906s.

Ngulani, T., and C.M. Shackleton. 2019. “Use of Public Urban Green Spaces for Spiritual Services in Bulawayo, Zimbabwe.” Urban Forestry & Urban Greening 38 (February): 97–104. https://doi.org/10.1016/j.ufug.2018.11.009.

Nicholls, C.I., and M.A. Altieri. 2013. “Plant Biodiversity Enhances Bees and Other Insect Pollinators in Agroecosystems: A Review.” Agronomy for Sustainable Development 33 (April): 257–74. https://doi.org/10.1007/s13593-012-0092-y.

Nicolaou, L., and W. Checkley. 2021. “Inequities in Air Pollution Exposure and Gaps in Air Quality Monitoring.” Journal of Allergy and Clinical Immunology 148 (1): 64–66. https://www.jacionline.org/article/S0091-6749(21)00653-9/abstract.

Nieuwenhuijsen, M.J. 2018. “Influence of Urban and Transport Planning and the City Environment on Cardiovascular Disease.” Nature Reviews Cardiology 15 (7): 432–38. https://doi.org/10.1038/s41569-018-0003-2.

Nieuwenhuijsen, M.J., H. Khreis, M. Triguero-Mas, M. Gascon, and P. Dadvand. 2017. “Fifty Shades of Green.” Epidemiology 28 (1): 63–71. https://doi.org/10.1097/EDE.0000000000000549.

NOAA (National Oceanic and Atmospheric Administration). 2021. “It’s Official: July Was Earth’s Hottest Month on Record.” August 13. https://www.noaa.gov/news/its-official-july-2021-was-earths-hottest-month-on-record.

NOAA. n.d. “Air-Sea Fluxes.” Ocean Climate Stations. https://www.pmel.noaa.gov/ocs/air-sea-fluxes. Accessed May 6, 2020.

Nobre, C.A., and L.D.S. Borma. 2009. “‘Tipping Points’ for the Amazon Forest.” Current Opinion in Environmental Sustainability 1 (1): 28–36. https://doi.org/10.1016/j.cosust.2009.07.003.

Nowak, D.J., N. Appleton, A. Ellis, and E. Greenfield. 2017. “Residential Building Energy Conservation and Avoided Power Plant Emissions by Urban and Community Trees in the United States.” Urban Forestry & Urban Greening 21 (January): 158–65. https://doi.org/10.1016/j.ufug.2016.12.004.

Nowak, D.J., and D.E. Crane. 2002. “Carbon Storage and Sequestration by Urban Trees in the USA.” Environmental Pollution 116 (3): 381–89. https://doi.org/10.1016/S0269-7491(01)00214-7.

Nowak, D.J., and J.F. Dwyer. 2007. “Understanding the Benefits and Costs of Urban Forest Ecosystems.” In Urban and Community Forestry in the Northeast, edited by J.E. Kuser, 25–46. Dordrecht: Springer Netherlands. https://doi.org/10.1007/978-1-4020-4289-8_2.

Nowak, D.J., and E.J. Greenfield. 2018a. “Declining Urban and Community Tree Cover in the United States.” Urban Forestry & Urban Greening 32 (May): 32–55. https://doi.org/10.1016/j.ufug.2018.03.006.

Nowak, D.J., and E.J. Greenfield. 2018b. “US Urban Forest Statistics, Values, and Projections.” Journal of Forestry 116 (2): 164–77. https://doi.org/10.1093/jofore/fvx004.

Nowak, D.J., and E.J. Greenfield. 2020. “The Increase of Impervious Cover and Decrease of Tree Cover within Urban Areas Globally (2012–2017).” Urban Forestry & Urban Greening 49 (March): 126638. https://doi.org/10.1016/j.ufug.2020.126638.

Nowak, D.J., E.J. Greenfield, and R.M. Ash. 2019. “Annual Biomass Loss and Potential Value of Urban Tree Waste in the United States.” Urban Forestry & Urban Greening 46 (December): 126469. https://doi.org/10.1016/j.ufug.2019.126469.

Nowak, D.J., E.J. Greenfield, R.E. Hoehn, and E. Lapoint. 2013. “Carbon Storage and Sequestration by Trees in Urban and Community Areas of the United States.” Environmental Pollution 178 (July): 229–36. https://doi.org/10.1016/j.envpol.2013.03.019.

Nowak, D.J., S. Hirabayashi, A. Bodine, and E. Greenfield. 2014. “Tree and Forest Effects on Air Quality and Human Health in the United States.” Environmental Pollution 193 (October): 119–29. https://doi.org/10.1016/j.envpol.2014.05.028.

Nowak, D.J., J.C. Stevens, S.M. Sisinni, and C.J. Luley. 2002. “Effects of Urban Tree Management and Species Selection on Atmospheric Carbon Dioxide.” Journal of Arboriculture 28 (3). https://www.fs.usda.gov/treesearch/pubs/18815.

NPS (National Park Service). 2019. “Yellowstone National Park: Park Facts.” https://www.nps.gov/yell/planyourvisit/parkfacts.htm.

NRC (National Research Council). 1999. “The Values of Biodiversity.” Chapter 3 of Perspectives on Biodiversity: Valuing Its Role in an Everchanging World. Washington, DC: National Academies Press. https://www.ncbi.nlm.nih.gov/books/NBK224412/.

Nussbaumer, T. 2003. “Combustion and Co-combustion of Biomass: Fundamentals, Technologies, and Primary Measures for Emission Reduction.” Energy Fuels 17 (6): 1510–21. https://doi.org/10.1021/ef030031q.

Nwanevu, O. 2019. “A New Generation of Activists Confronts the Extinction Crisis.” New Yorker, May 13. https://www.newyorker.com/news/our-columnists/a-new-generation-of-activists-confronts-the-extinction-crisis.

NYC (New York City) Audubon. n.d. “Our Work: Conservation.” http://nycaudubon.org/conservation. Accessed September 3, 2020.

NYC (New York City) Department of Parks & Recreation. n.d. “Gardening with New York City Native Plants.” https://naturalareasnyc.org/media/pages/in-print/research/8cf424230f-1601408873/nrg_publication_gardening_with_nyc_native_plants.pdf. Accessed September 3, 2020.

O’Brien, L., R. De Vreese, M. Kern, T. Sievanen, B. Stojanova, and E. Atmis. 2017. “Cultural Ecosystem Benefits of Urban and Peri-urban Green Infrastructure across Different European Countries.” Urban Forestry & Urban Greening 24 (May): 236–48. https://doi.org/10.1016/j.ufug.2017.03.002.

Öckinger, E., and H.G. Smith. 2007. "Semi-natural Grasslands as Population Sources for Pollinating Insects in Agricultural Landscapes.” Journal of Applied Ecology 44 (1): 50–59. https://doi.org/10.1111/j.1365-2664.2006.01250.x.

Oh, B., K.J. Lee, C. Zaslawski, A. Yeung, D. Rosenthal, L. Larkey, and M. Back. 2017. “Health and Well-Being Benefits of Spending Time in Forests: Systematic Review.” Environmental Health and Preventive Medicine 22 (October): 71. https://doi.org/10.1186/s12199-017-0677-9.

Okyerefo, M.P.K., and D.Y. Fiaveh. 2017. “Prayer and Health-Seeking Beliefs in Ghana: Understanding the ‘Religious Space’ of the Urban Forest.” Health Sociology Review 26 (3): 308–20. https://doi.org/10.1080/14461242.2016.1257360.

Oliver, C.D., N.T. Nassar, B.R. Lippke, and J.B. McCarter. 2014. “Carbon, Fossil Fuel, and Biodiversity Mitigation with Wood and Forests.” Journal of Sustainable Forestry 33 (3): 248–75. https://doi.org/10.1080/10549811.2013.839386.

Oliver, T.H., M.S. Heard, N.J.B. Isaac, D.B. Roy, D. Procter, F. Eigenbrod, R. Freckleton, et al. 2015. “Biodiversity and Resilience of Ecosystem Functions.” Trends in Ecology & Evolution 30 (11): 673–84. https://doi.org/10.1016/j.tree.2015.08.009.

Olivero, J., J.E. Fa, R. Real, A.L. Márquez, M.A. Farfán, J.M. Vargas, D. Gaveau, et al. 2017. "Recent Loss of Closed Forests Is Associated with Ebola Virus Disease Outbreaks.” Scientific Reports 7 (October): 14291. https://doi.org/10.1038/s41598-017-14727-9.

Ollerton, J. 2017. “Pollinator Diversity: Distribution, Ecological Function, and Conservation.” Annual Review of Ecology, Evolution, and Systematics 48 (1): 353–76. https://doi.org/10.1146/annurev-ecolsys-110316-022919.

Ollerton, J., R. Winfree, and S. Tarrant. 2011. “How Many Flowering Plants Are Pollinated by Animals?” Oikos 120 (3): 321–26. https://doi.org/10.1111/j.1600-0706.2010.18644.x.

Olsson, L., H. Barbosa, S. Bhadwal, A. Cowie, K. Delusca, D. Flores-Renteria, K. Hermans, et al. 2019. “Land Degradation.” In Climate Change and Land: An IPCC Special Report on Climate Change, Desertification, Land Degradation, Sustainable Land Management, Food Security, and Greenhouse Gas Fluxes in Terrestrial Ecosystems, edited by P.R. Shukla, J. Skea, E. Calvo Buendia, V. Masson-Delmotte, H.-O. Pörtner, D.C. Roberts, P. Zhai, et al., 345–46. Cambridge and New York: Cambridge University Press. https://www.ipcc.ch/site/assets/uploads/sites/4/2019/11/07_Chapter-4.pdf.

Oppenheimer, M., B.C. Glavovic, J. Hinkel, R. van de Wal, A.K. Magnan, A. Abd-Elgawad, R. Cai, et al. 2019b. “Sea Level Rise and Implications for Low-Lying Islands, Coasts and Communities.” In IPCC Special Report on the Ocean and Cryosphere in a Changing Climate, edited by H.-O. Pörtner, D.C. Roberts, V. Masson-Delmotte, P. Zhai, M. Tignor, E. Poloczanska, K. Mintenbeck, et al., 321–45. Cambridge and New York: Cambridge University Press. https://doi.org/10.1017/9781009157964.006.

Ordóñez, C., and P.N. Duinker. 2013. “An Analysis of Urban Forest Management Plans in Canada: Implications for Urban Forest Management.” Landscape and Urban Planning 116 (August): 36–47. https://doi.org/10.1016/j.landurbplan.2013.04.007.

O’Sullivan, F. 2017. “Built-Out Barcelona Makes Space for an Urban Forest.” Bloomberg CityLab, May 17. https://www.bloomberg.com/news/articles/2017-05-17/how-built-out-barcelona-found-space-for-an-urban-forest.

Ozment, S., R. Feltran-Barbieri, P. Hamel, E. Gray, J. Baladelli Ribeiro, S. Roiphe Barreto, A. Padovezi, and T. Piazzetta Valente. 2018. Natural Infrastructure in São Paulo's Water System. Washington, DC: World Resources Institute. https://www.wri.org/research/natural-infrastructure-sao-paulos-water-system.

Pan, Y., R.A. Birdsey, J. Fang, R. Houghton, P.E. Kauppi, W.A. Kurz, O.L. Phillips, et al. 2011. “A Large and Persistent Carbon Sink in the World’s Forests.” Science 333 (6045): 988–93. https://doi.org/10.1126/science.1201609.

Parks, R., M. McLaren, R. Toumi, and U. Rivett. 2019. “Experiences and Lessons in Managing Water from Cape Town.” Grantham Institute Briefing Paper 29. London: Grantham Institute, Imperial College London. https://www.researchgate.net/publication/336681159_Experiences_and_lessons_in_managing_water_from_Cape_Town.

Parque Nacional da Serra dos Orgãos. n.d. "Atributos Naturais.” Accessed May 11, 2021. https://www.icmbio.gov.br/parnaserradosorgaos/atributos-naturais.html.

Parque Nacional da Tijuca. n.d. "Informações Gerais." Accessed May 11, 2021. https://www.icmbio.gov.br/parnatijuca/informacoes-gerais.html.

Pataki, D.E., M.M. Carreiro, J. Cherrier, N.E. Grulke, V. Jennings, S. Pincetl, R.V. Pouyat, T.H. Whitlow, and W.C. Zipperer. 2011a. “Coupling Biogeochemical Cycles in Urban Environments: Ecosystem Services, Green Solutions, and Misconceptions.” Frontiers in Ecology and the Environment 9 (1): 27–36. https://doi.org/10.1890/090220.

Payn, T., J.-M. Carnus, P. Freer-Smith, M. Kimberley, W. Kollert, S. Liu, C. Orazio, L. Rodriguez, L.N. Silva, and M.J. Wingfield. 2015. “Changes in Planted Forests and Future Global Implications.” In “Changes in Global Forest Resources from 1990 to 2015,” edited by K. MacDicken, special issue, Forest Ecology and Management 352 (September): 57–67. https://doi.org/10.1016/j.foreco.2015.06.021.

Pearce, F. 2018. “Conflicting Data: How Fast Is the World Losing Its Forests?” Yale Environment 360. October 9. https://e360.yale.edu/features/conflicting-data-how-fast-is-the-worlds-losing-its-forests.

Pearson, T.R.H., S. Brown, L. Murray, and G. Sidman. 2017. “Greenhouse Gas Emissions from Tropical Forest Degradation: An Underestimated Source.” Carbon Balance and Management 12 (February): 3. https://doi.org/10.1186/s13021-017-0072-2.

Peen, J., R.A. Schoevers, A.T. Beekman, and J. Dekker. 2010. “The Current Status of Urban-Rural Differences in Psychiatric Disorders.” Acta Psychiatrica Scandinavica 121 (2): 84–93. https://doi.org/10.1111/j.1600-0447.2009.01438.x.

Pendrill, F., U.M. Persson, J. Godar, and T. Kastner. 2019. “Deforestation Displaced: Trade in Forest-Risk Commodities and the Prospects for a Global Forest Transition.” Environmental Research Letters 14 (5): 055003. https://doi.org/10.1088/1748-9326/ab0d41.

Pendrill, F., U.M. Persson, J. Godar, T. Kastner, D. Moran, S. Schmidt, and R. Wood. 2019. “Agricultural and Forestry Trade Drives Large Share of Tropical Deforestation Emissions.” Global Environmental Change 56 (May): 1–10. https://doi.org/10.1016/j.gloenvcha.2019.03.002.

Perez-Aleman, P., and M. Sandilands. 2008. “Building Value at the Top and the Bottom of the Global Supply Chain: MNC-NGO Partnerships.” California Management Review 51 (1): 24–49. https://doi.org/10.2307/41166467.

Phelan, P.E., K. Kaloush, M. Miner, J. Golden, B. Phelan, H. Silva, and R.A. Taylor. 2015. “Urban Heat Island: Mechanisms, Implications, and Possible Remedies.” Annual Review of Environment and Resources 40 (1): 285–307. https://doi.org/10.1146/annurev-environ-102014-021155.

Phillips, M., S.B. Francisco, S. Wilson, P. Langer, L. Jarvis, and N. Garcia. Forthcoming. “Forest Footprint for Cities: Methods for Estimating Deforestation and Associated CO₂ Emissions Embodied in Products Consumed in Cities.” Technical Note. Washington, DC: World Resources Institute.

Phillips, T.H., M.E. Baker, K. Lautar, I. Yesilonis, and M.A. Pavao-Zuckerman. 2019. “The Capacity of Urban Forest Patches to Infiltrate Stormwater Is Influenced by Soil Physical Properties and Soil Moisture.” Journal of Environmental Management 246 (September): 11–18. https://doi.org/10.1016/j.jenvman.2019.05.127.

Pimm, S.L., C.N. Jenkins, R. Abell, T.M. Brooks, J.L. Gittleman, L.N. Joppa, P.H. Raven, C.M. Roberts, and J.O. Sexton. 2014. “The Biodiversity of Species and Their Rates of Extinction, Distribution, and Protection.” Science 344 (6187). https://doi.org/10.1126/science.1246752.

Piotto, D., D. Craven, F. Montagnini, and A. Federico. 2010. “Silvicultural and Economic Aspects of Pure and Mixed Native Tree Species Plantations on Degraded Pasturelands in Humid Costa Rica.” New Forests 39 (May): 369–85. https://doi.org/10.1007/s11056-009-9177-0

Poe, M.R., R.J. McLain, M. Emery, and P.T. Hurley. 2013. “Urban Forest Justice and the Rights to Wild Foods, Medicines, and Materials in the City.” Human Ecology 41 (June): 409–22. https://doi.org/10.1007/s10745-013-9572-1.

Pool, J.R., D. Gibbs, S. Alexander, and N. Harris. 2022. “5 Reasons Cities Should Include Trees in Climate Action” Insights (blog), July 28. https://www.wri.org/insights/urban-trees-city-climate-action.

Poorter, L., F. Bongers, T.M. Aide, A.M. Almeyda Zambrano, P. Balvanera, J.M. Becknell, V. Boukili, et al. 2016. “Biomass Resilience of Neotropical Secondary Forests.” Nature 530 (7589): 211–14. https://doi.org/10.1038/nature16512.

Poorter, L., M.T. van der Sande, J. Thompson, E.J.M.M. Arets, A. Alarcón, J. Álvarez-Sánchez, N. Ascarrunz, et al. 2015. “Diversity Enhances Carbon Storage in Tropical Forests: Carbon Storage in Tropical Forests.” Global Ecology and Biogeography 24 (11): 1314–28. https://doi.org/10.1111/geb.12364.

Postel, S.L., and B.H. Thompson. 2005. “Watershed Protection: Capturing the Benefits of Nature’s Water Supply Services.” Natural Resources Forum 29 (2): 98–108. https://doi.org/10.1111/j.1477-8947.2005.00119.x.

Potgieter, L.J., M. Gaertner, C. Kueffer, B.M.H. Larson, S.W. Livingstone, P.J. O’Farrell, and D.M. Richardson. 2017. “Alien Plants as Mediators of Ecosystem Services and Disservices in Urban Systems: A Global Review.” Biological Invasions 19 (December): 3571–88. https://doi.org/10.1007/s10530-017-1589-8.

Potts, S.G., J.C. Biesmeijer, C. Kremen, P. Neumann, O. Schweiger, and W.E. Kunin. 2010. “Global Pollinator Declines: Trends, Impacts and Drivers.” Trends in Ecology & Evolution 25 (6): 345–53. https://doi.org/10.1016/j.tree.2010.01.007.

Potts, S.G., V. Imperatriz-Fonseca, H.T. Ngo, M.A. Aizen, J.C. Biesmeijer, T.D. Breeze, L.V. Dicks, et al. 2016. “Safeguarding Pollinators and Their Values to Human Well-Being.” Nature 540 (December): 220–29. https://doi.org/10.1038/nature20588.

Potvin, C., L. Mancilla, N. Buchmann, J. Monteza, T. Moore, M. Murphy, Y. Oelmann, et al. 2011. “An Ecosystem Approach to Biodiversity Effects: Carbon Pools in a Tropical Tree Plantation.” In “The Ecology and Ecosystem Services of Native Trees: Implications for Reforestation and Land Restoration in Mesoamerica,” edited by J.S. Hall, M.S. Ashton, and E.J. Garen, special issue, Forest Ecology and Management 261 (10): 1614–24. https://doi.org/10.1016/j.foreco.2010.11.015.

Pougy, N., E. Martins, M. Verdi, J. Oliveira, D. Maurenza, R. Amaro, and G. Martinelli. 2014. “Urban Forests and the Conservation of Threatened Plant Species: The Case of the Tijuca National Park, Brazil.” Natureza & Conservação 12 (2): 170–73. https://doi.org/10.1016/j.ncon.2014.09.007.

Pozo, P., and I. Säumel. 2018. "How to Bloom the Green Desert: Eucalyptus Plantations and Native Forests in Uruguay beyond Black and White Perspectives.” Forests 9 (10): 614. https://doi.org/10.3390/f9100614.

Pramova, E., B. Locatelli, H. Djoudi, and O.A. Somorin. 2012. “Forests and Trees for Social Adaptation to Climate Variability and Change.” Wiley Interdisciplinary Reviews Climate Change 3 (6): 581–96. https://doi.org/10.1002/wcc.195.

Pregitzer, C.C., S. Charlop-Powers, C. McCabe, A. Hiple, B. Gunther, and M.A. Bradford. 2019. Untapped Common Ground: The Care of Forested Natural Areas in American Cities. New York: Natural Areas Conservancy. https://naturalareasnyc.org/content/national/nac_careofurbannature_lores-singles.pdf?1553522646.

Pregitzer, K.S., and E.S. Euskirchen. 2004. “Carbon Cycling and Storage in World Forests: Biome Patterns Related to Forest Age.” Global Change Biology 10 (12): 2052–77. https://doi.org/10.1111/j.1365-2486.2004.00866.x.

Prevedello, J.A., M. Almeida-Gomes, and D.B. Lindenmayer. 2017. “The Importance of Scattered Trees for Biodiversity Conservation: A Global Meta-analysis.” Journal of Applied Ecology 55 (1). https://doi.org/10.1111/1365-2664.12943.

Pugh, T.A.M., M. Lindeskog, B. Smith, B. Poulter, A. Arneth, V. Haverd, and L. Calle. 2019. “Role of Forest Regrowth in Global Carbon Sink Dynamics.” Proceedings of the National Academy of Sciences of the United States of America 116 (10): 4382–87. https://doi.org/10.1073/pnas.1810512116.

Pugh, T.A.M., A.R. MacKenzie, J.D. Whyatt, and C.N. Hewitt. 2012. “Effectiveness of Green Infrastructure for Improvement of Air Quality in Urban Street Canyons.” Environmental Science & Technology 46 (14): 7692–99. https://doi.org/10.1021/es300826w.

PUB (Public Utilities Board). 2022. “Singapore Water Story.” January 10. https://www.pub.gov.sg/watersupply/singaporewaterstory#:~:text=Water%20demand%20in%20Singapore%20is,sector%20taking%20up%20the%20rest.

PWD (Philadelphia Water Department). 2011. Green City, Clean Waters: The City of Philadelphia’s Program for Combined Sewage Overflow Control Program Summary. Amended. Philadelphia: PWD. http://archive.phillywatersheds.org/doc/GCCW_AmendedJune2011_LOWRES-web.pdf.

PWD. n.d. “Stormwater.” https://water.phila.gov/stormwater/. Accessed September 7, 2022.

Qin, Y., and T. Gartner. 2016. “Watersheds Lost Up to 22% of Their Forests in 14 Years. Here’s How It Affects Your Water Supply.” Insights (blog), August 30. https://www.wri.org/insights/watersheds-lost-22-their-forests-14-years-heres-how-it-affects-your-water-supply.

Rainforest Foundation Norway. 2012. Rainforest Foundation Norway Annual Report 2012. Oslo: Rainforest Foundation Norway. https://d5i6is0eze552.cloudfront.net/documents/Publikasjoner/Aarsmeldinger/Annual-Report-2012.pdf?mtime=20150905163958.

Randrup, T.B., E.G. McPherson, and L.R. Costello. 2001. “A Review of Tree Root Conflicts with Sidewalks, Curbs, and Roads.” Urban Ecosystems 5 (September): 209–25. https://doi.org/10.1023/A:1024046004731.

Raupp, M., A. Buckelew, and E. Raupp. 2006. “Street Tree Diversity in Eastern North America and Its Potential for Tree Loss to Exotic Borers.” Arboriculture and Urban Forestry 32 (6): 297–304. https://pubag.nal.usda.gov/catalog/27863.

Reid, W.V., and K. Miller. 1989. Keeping Options Alive: The Scientific Basis for Conserving Biodiversity. Washington, DC: World Resources Institute.

Revi, A., D.E. Satterthwaite, F. Aragón-Durand, J. Corfee-Morlot, R.B.R. Kiunsi, M. Pelling, D.C. Roberts, and W. Solecki. 2014b. “Urban Areas.” In Climate Change 2014: Impacts, Adaptation, and Vulnerability. Part A: Global and Sectoral Aspects. Contribution of Working Group II to the Fifth Assessment Report of the Intergovernmental Panel on Climate Change, edited by C.B. Field, V.R. Barros, D.J. Dokken, K.J. Mach, M.D. Mastrandrea,T.E. Bilir, M. Chatterjee, et al., 535–612. Cambridge and New York: Cambridge University Press. https://www.ipcc.ch/site/assets/uploads/2018/02/WGIIAR5-Chap8_FINAL.pdf.

Reynolds, C.C., F.J. Escobedo, N. Clerici, and J. Zea-Camaño. 2017. "Does 'Greening' of Neotropical Cities Considerably Mitigate Carbon Dioxide Emissions? The Case of Medellin, Colombia." Sustainability 9 (5): 785. https://doi.org/10.3390/su9050785.

Ribeiro, M.C., A.C. Martensen, J.P. Metzger, M. Tabarelli, F. Scarano, and M.-J. Fortin. 2011. “The Brazilian Atlantic Forest: A Shrinking Biodiversity Hotspot.” In Biodiversity Hotspots: Distribution and Protection of Conservation Priority Areas, edited by F. Zachos and J. Habel, 405–34. Berlin: Springer. https://doi.org/10.1007/978-3-642-20992-5_21.

Richardson, J.S., and S. Béraud. 2014. "Effects of Riparian Forest Harvest on Streams: A Meta-analysis.” Journal of Applied Ecology 51 (6): 1712–21. https://doi.org/10.1111/1365-2664.12332.

Robine, J.-M., S.L.K. Cheung, S. Le Roy, H. Van Oyen, C. Griffiths, J.-P. Michel, and F.R. Herrmann. 2008. “Death Toll Exceeded 70,000 in Europe during the Summer of 2003.” Comptes Rendus Biologies 331 (2): 171–78. https://doi.org/10.1016/j.crvi.2007.12.001.

Robinson, M.M., and X. Zhang. 2011. The World Medicines Situation 2011: Traditional Medicines— Global Situation, Issues and Challenges. Geneva: World Health Organization.

Rojas-Rueda, D., M.J. Nieuwenhuijsen, M. Gascon, D. Perez-Leon, and P. Mudu. 2019. “Green Spaces and Mortality: A Systematic Review and Meta-analysis of Cohort Studies.” Lancet Planetary Health 3 (11): e469–77. https://doi.org/10.1016/S2542-5196(19)30215-3.

Roman, L.A., J.J. Battles, and J.R. McBride. 2014. “The Balance of Planting and Mortality in a Street Tree Population.” Urban Ecosystems 17 (2): 387–404. https://doi.org/10.1007/s11252-013-0320-5.

Roman, L.A., and F.N. Scatena. 2011. “Street Tree Survival Rates: Meta-analysis of Previous Studies and Application to a Field Survey in Philadelphia, PA, USA.” Urban Forestry & Urban Greening 10 (4): 269–74. https://doi.org/10.1016/j.ufug.2011.05.008.

Rook, G.A. 2013. “Regulation of the Immune System by Biodiversity from the Natural Environment: An Ecosystem Service Essential to Health.” Proceedings of the National Academy of Sciences of the United States of America 110 (46): 18360–67. https://doi.org/10.1073/pnas.1313731110.

Room & Board. 2018. “Salvaging Baltimore with the USDA Forest Service.” June 9. https://www.roomandboard.com/blog/2018/06/salvaging-baltimore-with-the-usda-forest-service/.

Rosa, C.D., C.C. Profice, and S. Collado. 2018. “Nature Experiences and Adults’ Self-Reported Pro-environmental Behaviors: The Role of Connectedness to Nature and Childhood Nature Experiences.” Frontiers in Psychology 9. https://doi.org/10.3389/fpsyg.2018.01055.

Rosenzweig, B.R., L. McPhillips, H. Chang, C. Cheng, C. Welty, M. Matsler, D. Iwaniec, and C.I. Davidson. 2018. “Pluvial Flood Risk and Opportunities for Resilience.” Wiley Interdisciplinary Reviews Water 5 (6): e1302. https://doi.org/10.1002/wat2.1302.

Roy, S., J. Byrne, and C. Pickering. 2012. “A Systematic Quantitative Review of Urban Tree Benefits, Costs, and Assessment Methods across Cities in Different Climatic Zones.” Urban Forestry & Urban Greening 11 (4): 351–63. https://doi.org/10.1016/j.ufug.2012.06.006.

SaferSpaces. n.d. “Safe and Inclusive Parks in the Johannesburg Inner-City.” https://www.saferspaces.org.za/be-inspired/entry/inner-city-safer-parks-and-open-spaces-strategic-framework-end-street-north. Accessed December 12, 2020.

Salbitano, F., S. Borelli, M. Conigliaro, and Y. Chen. 2016. “Guidelines on Urban and Peri-urban Forestry.” Forestry Paper 178. Rome: Food and Agriculture Organization of the United Nations.

Salbitano, F., S. Borelli, M. Conigliaro, N.A. Yahya, G. Sanesi, Y. Chen, and G.T. Corzo. 2017. “Urban Forest Benefits in Developing and Industrializing Countries.” In Routledge Handbook of Urban Forestry, edited by F. Ferrini, C.C. Konijnendijk van den Bosch, and A. Fini. London: Routledge. https://doi.org/10.4324/9781315627106.ch10.

Salkeld, D.J., K.A. Padgett, and J.H. Jones. 2013. “A Meta-analysis Suggesting That the Relationship between Biodiversity and Risk of Zoonotic Pathogen Transmission Is Idiosyncratic.” Ecology Letters 16 (5): 679–86. https://doi.org/10.1111/ele.12101.

Salmond, J.A., M. Tadaki, S. Vardoulakis, K. Arbuthnott, A. Coutts, M. Demuzere, K.N. Dirks, et al. 2016. “Health and Climate Related Ecosystem Services Provided by Street Trees in the Urban Environment.” Environmental Health 15 (Suppl 1): S36. https://doi.org/10.1186/s12940-016-0103-6.

Sampaio, M.B., M.F. De La Fuente, U.P. Albuquerque, A. da Silva Souto, and N. Schiel. 2018. “Contact with Urban Forests Greatly Enhances Children’s Knowledge of Faunal Diversity.” Urban Forestry & Urban Greening 30 (March): 56–61. https://doi.org/10.1016/j.ufug.2018.01.006.

Sandifer, P.A., A.E. Sutton-Grier, and B.P. Ward. 2015. “Exploring Connections among Nature, Biodiversity, Ecosystem Services, and Human Health and Well-Being: Opportunities to Enhance Health and Biodiversity Conservation.” Ecosystem Services 12 (April): 1–15. https://doi.org/10.1016/j.ecoser.2014.12.007.

Santamour, F.S. 2004. “Trees for Urban Planting: Diversity, Uniformity, and Common Sense.” In The Overstory Book: Cultivating Connections with Trees, edited by C.R. Elevitch, 2nd ed., 396–99. Holualoa, Hawaii: Permanent Agriculture Resources. http://www.agroforestry.net.

Sarath Chandran, M.A., A.V.M. Subba Rao, V.M. Sandeep, V.P. Pramod, P. Pani, V.U.M. Rao, V. Visha Kumari, and C. Srinivasa Rao. 2017. “Indian Summer Heat Wave of 2015: A Biometeorological Analysis Using Half Hourly Automatic Weather Station Data with Special Reference to Andhra Pradesh.” International Journal of Biometeorology 61 (June): 1063–72. https://doi.org/10.1007/s00484-016-1286-9.

Sassen, M., D. Sheil, and K.E. Giller. 2015. “Fuelwood Collection and Its Impacts on a Protected Tropical Mountain Forest in Uganda.” Forest Ecology and Management 354 (October): 56–67. https://doi.org/10.1016/j.foreco.2015.06.037.

Säumel, I., F. Weber, and I. Kowarik. 2016. “Toward Livable and Healthy Urban Streets: Roadside Vegetation Provides Ecosystem Services Where People Live and Move.” Environmental Science & Policy 62 (August): 24–33. https://doi.org/10.1016/j.envsci.2015.11.012.

Schwarz, K., M. Fragkias, C.G. Boone, W. Zhou, M. McHale, J.M. Grove, J. O’Neil-Dunne, et al. 2015. “Trees Grow on Money: Urban Tree Canopy Cover and Environmental Justice.” PLoS ONE 10 (4): e0122051. https://doi.org/10.1371/journal.pone.0122051.

Searcey, D. 2018. “Across Senegal, the Beloved Baobab Tree Is the ‘Pride of the Neighborhood.’” New York Times, September 30. https://www.nytimes.com/2018/09/30/world/africa/senegal-baobabs-climate-change.html.

Searchinger, T., and R. Heimlich. 2015. “Avoiding Bioenergy Competition for Food Crops and Land.” Working Paper. Washington, DC: World Resources Institute. https://www.wri.org/research/avoiding-bioenergy-competition-food-crops-and-land.

Searchinger, T., J. Zionts, L. Peng, and R. Waite. Forthcoming. “The Global Land Squeeze: Managing the Growing Competition for Land.” Washington, DC: World Resources Institute.

Searchinger, T.D., T. Beringer, B. Holtsmark, D.M. Kammen, E.F. Lambin, W. Lucht, P. Raven, and J.-P. van Ypersele. 2018. “Europe’s Renewable Energy Directive Poised to Harm Global Forests.” Nature Communications 9 (1): 3741. https://doi.org/10.1038/s41467-018-06175-4.

Searchinger, T.D., S.P. Hamburg, J. Melillo, W. Chameides, P. Havlik, D.M. Kammen, G.E. Likens, et al. 2009. “Fixing a Critical Climate Accounting Error.” Science 326 (5952): 527–28. https://doi.org/10.1126/science.1178797.

Seddon, N., A. Chausson, P. Berry, C.A.J. Girardin, A. Smith, and B. Turner. 2020. “Understanding the Value and Limits of Nature-Based Solutions to Climate Change and Other Global Challenges.” Philosophical Transactions of the Royal Society B: Biological Sciences 375 (1794): 20190120. https://doi.org/10.1098/rstb.2019.0120.

Seddon, N., B. Turner, P. Berry, A. Chausson, and C.A.J. Girardin. 2019. “Grounding Nature-Based Climate Solutions in Sound Biodiversity Science.” Nature Climate Change 9 (2): 84–87. https://doi.org/10.1038/s41558-019-0405-0.

SEDEMA (Secretaría del Medio Ambiente). n.d. “Explora el Arbolado de la 1ra Sección del Bosque de Chapultepec." http://www.data.sedema.cdmx.gob.mx/arboladochapultepec/. Accessed June 13, 2022.

Sen, T., and S.K. Samanta. 2015. “Medicinal Plants, Human Health and Biodiversity: A Broad Review.” In Biotechnological Applications of Biodiversity, edited by J. Mukherjee, 59–110. Berlin: Springer. https://doi.org/10.1007/10_2014_273.

Seneviratne, S.I., N. Nicholls, D. Easterling, C.M. Goodess, S. Kanae, J. Kossin, Y. Luo, et al. 2012. “Changes in Climate Extremes and Their Impacts on the Natural Physical Environment.” In Managing the Risks of Extreme Events and Disasters to Advance Climate Change Adaptation: A Special Report of Working Groups I and II of the Intergovernmental Panel on Climate Change, edited by C.B. Field, V. Barros, T.F. Stocker, D. Qin, D.J. Dokken, K.L. Ebi, M.D. Mastrandrea, et al., 109–230. Cambridge and New York: Cambridge University Press. https://doi.org/10.1017/CBO9781139177245.006.

Sengupta, S. 2019. “Protesting Climate Change, Young People Take to Streets in a Global Strike.” New York Times, September 21. https://www.nytimes.com/2019/09/20/climate/global-climate-strike.html.

Seto, K.C., S. Dhakal, A. Bigio, H. Blanco, G.C. Delgado, D. Dewar, L. Huang, et al. 2014. “Human Settlements, Infrastructure and Spatial Planning.” In Climate Change 2014: Mitigation of Climate Change. Contribution of Working Group III to the Fifth Assessment Report of the Intergovernmental Panel on Climate Change, edited by O. Edenhofer, R. Pichs-Madruga, Y. Sokona, E. Farahani, S. Kadner, K. Seyboth, A. Adler, et al., 923–1000. Cambridge and New York: Cambridge University Press. https://www.ipcc.ch/site/assets/uploads/2018/02/ipcc_wg3_ar5_chapter12.pdf.

Seto, K.C., M. Fragkias, B. Güneralp, and M.K. Reilly. 2011. “A Meta-analysis of Global Urban Land Expansion.” PLoS ONE 6 (8): e23777. https://doi.org/10.1371/journal.pone.0023777.

Seymour, F., and J. Busch. 2016. Why Forests? Why Now? The Science, Economics, and Politics of Tropical Forests and Climate Change. Washington, DC: Center for Global Development.

Seymour, F., and P. Langer. 2021. “Consideration of Nature-Based Solutions as Offsets in Corporate Climate Change Mitigation Strategies.” Working Paper. Washington, DC: World Resources Institute. https://doi.org/10.46830/wriwp.20.00043.

Seymour, F., and B. Morris. 2018. “Ending Tropical Deforestation: The Global Debate about Biofuels and Land-Use Change.” Working Paper. Washington, DC: World Resources Institute.