More than 80% of Americans and more than 65% of the global human population are expected to live in urban areas by 2050 (USDC 2014, United Nations 2014). Accommodating for this influx, the amount of “urban” land cover is projected to triple by 2030 (Seto et al. 2011, 2012). Based on past trends (McDonnell and Pickett 1997, Collins et al. 2000, Alberti et al. 2003, Duh et al. 2008), the interplay of socioeconomic and ecological factors will influence development outcomes and what urban landscapes look like over time. Strategies exist to balance ecological sustainability and urban human infrastructure (Ahern 2013), and research is exploring such linkages (e.g., Morzillo and Schwartz 2011, Londoño Cadavid 2013, Chang et al. 2014, Everett et al. 2016). Less is known, however, about the integrated role of human governance and land-use planning strategies and resulting impacts on the social and ecological resilience of urban landscapes.
Cities evolve as a result of independent yet interacting choices by humans at multiple scales within a biophysical framework (Collins et al. 2011), producing different landscape patterns with unique biophysical properties (e.g., Pickett and McDonnell 1993, Pickett et al. 2001, Grimm et al. 2008). This complexity results from polycentric decision making among varying scales of governance (Ostrom 2010), ranging from broad institutional down to the individual resident, that correspond to changes of both ecosystem function and social perception of those functions (Elmqvist et al. 2013). However, open questions remain about how such interscalar social-ecological relationships interact to express environmental outcomes and decisions influencing environmental attributes and ecosystem services.
An essential aspect of urban social-ecological interactions is the individual resident: his/her perceptions of the urban environment around him/her, and how he/she is empowered by local governance structures. At the most basic level, resident population is the metric used to define city size (USDC 2014). Behaviors by this key subset of urban stakeholders at the property level translate into patterns across neighborhoods and urban landscapes (Kinzig et al. 2005, Cook et al. 2012, Belaire et al. 2014). Revealed and stated preference models (Champ et al. 2003, Freeman 2003) have suggested the influence of environmental characteristics, such as water quality (Netusil et al. 2014), open space proximity (Geoghegan 2002), trees (Donovan and Butry 2010), and green stormwater management (Ando and Freitas 2011), on property values. Relationships exist between socioeconomic profiles and personal preferences for urban characteristics (e.g., Muller 1982), which play a central role in determining where an individual chooses to live (Tiebout 1956). For example, although preference for an oasis front yard motif was expressed among all residents, “inmigrants” to Phoenix from the U.S. Southeast, Great Plains, and Intermountain West were more likely to choose neighborhoods with neighborhood community associations than inmigrants from the Northeast, Midwest, Southwest, and Pacific West (Martin et al. 2003). In this case, property-scale landscape preferences were not always consistent with neighborhood-scale governance preferences. Thus, we postulate that individual preferences vary across scales, influencing what urban landscapes look like over time.
We explored this supposition using a suite of urban natural resource and social landscape characteristics that may be important to residents. Portland (Oregon) and Vancouver (Washington) were explicitly chosen for comparison because the two cities have similar biophysical attributes, but over time have taken distinctly different forms of social and political governance. This metropolitan area consists of two million people and spans the boundary of two states divided by the Columbia River. Within a 50-mile radius are three national forests, two state forests, and many mountain, river, and beach recreation opportunities. Set between the Cascade and Coast mountain ranges, the region experiences a mild marine-influenced climate with summer drought and winter rains. The two cities are tightly linked by watersheds, airsheds, and commuter sheds. Interstate 5 connects and bisects both cities, along with major north-south and east-west railroads. Estimates suggest that the area will grow by approximately 1.5 million inhabitants by 2030 (USDC 2014). More broadly, this effort is one component of the Portland-Vancouver Urban Long-Term Research Area Exploratory (ULTRA-Ex) project, the objective of which is to understand how human and biophysical systems respond over time to disturbances in urban social-ecological systems.
Despite the similar geographies of Portland and Vancouver (two largest cities on the Oregon and Washington sides of the metropolitan area; populations approximately 600,000 and 165,000, respectively; USDC 2014), land-use planning histories have shaped regional urban development in Oregon and Washington (Kline et al. 2014). The Oregon Land Conservation and Development Act of 1973 included 19 goals to safeguard opportunity for natural resources extraction and to protect the economic value of agricultural production. Goal 14, “urbanization,” describes the establishment of and conditions for making changes to urban growth boundaries (UGBs) for each city in the state and requires state-approved comprehensive planning at the local level (Oregon Department of Land Conservation and Development 2006). In 1991, Washington passed the Growth Management Act that established UGBs to manage growth and protect open space in response to rapid development surrounding Puget Sound (Kline et al. 2014). Comparatively, Washington’s guidelines are less centralized with greater local-level management than Oregon’s. Although UGBs have contained development in both states (Kline et al. 2014, Lettman et al. 2014), it is unknown what role, if any, these differences, and factors such as tax policies, land-use planning decisions, natural resource preferences, and access to mass transit, have had on trends in social perspectives between Portland and Vancouver, including residential perspectives of urban natural resources.
Besides diverse state land-use histories, a general reputation for sustainability and greenness has been ascribed to Portland (Greenbiz 2008, Svoboda et al. 2008) when compared to neighboring Vancouver. Our working hypothesis is that the varying history of land-use governance and reputation for greenness are reflected in resident perceptions such that a greater number of Portland respondents would indicate importance for natural resource characteristics than Vancouver respondents (Table 1, H1). Support for this hypothesis in our study may illustrate ways in which institutional differences and land-use governance interact and are emulated by residential perceptions and behaviors. To test this hypothesis, we assessed the importance of 15 selected landscape characteristics for each city at three scales of analysis. Then, we applied both univariate and multivariate techniques to compare and contrast similarities and differences between the two cities. Finally, we considered three factors that may be attributed to differences in responses from each city and contribute to residential perspectives of the cities over time.
Our study extent included similar neighborhoods, both relatively close to and far from urban natural resources, such as streams and other green infrastructure. A mail survey was used for data collection. Our sampling unit was the individual household, and we defined our sampling frame as the list of residential street addresses within the study extent. Street address information was purchased from Marketing Systems Group (Fort Washington, PA), which compiles sampling datasets from U.S. Postal Service delivery sequence files. Single delivery points for multiple addresses, e.g., post office boxes and mail drops, were excluded to preserve spatial context. We also excluded apartment buildings to maximize representation of individuals who make decisions at the scale of individual residential lots.
We used multiple mailings in an effort to increase response rates (Dillman et al. 2009) and based the sample size on a desired sampling error of ± 5%. In 2012, we sent questionnaires to randomly selected households in Portland and Vancouver (n = 3000 each; N = 6000). A follow-up telephone survey (n = 132) of nonrespondents to the original survey revealed that the most common reason for nonresponse was not receiving the original survey (n = 64; 48%).
To evaluate the importance of landscape characteristics, respondents were asked to respond to 15 items as either “important” (1) or “not important” (0). These items included: (a) large mature trees; (b) tree-lined streets; (c) native vegetation; (d) vegetation that is attractive all year; (e) landscaping with low-cost maintenance; (f) reliably colorful flowers; (g) well-manicured vegetation; (h) streams or rivers; (i) vegetation along streams; (j) urban (landscaped) parks; (k) parks with trails and natural areas; (l) plentiful accessible parking; (m) natural stormwater management; (n) public transportation; and (o) stores and services. Responses to each item were indicated at three spatial scales. Consequently, we hypothesized that in each city, the percent of respondents who indicated the importance of each landscape characteristic would vary across scales (Table 1, H2).
First, the finest scale of analysis was the individual property-level scale, “at or next to my house.” Individual households are the fundamental unit of urban land management (Chowdhury et al. 2011) and the center of residential decision making (Shakeel and Conway 2014). Past research suggests that property-level decisions, such as landscaping preferences (e.g., Yabiku et al. 2008), may be associated with socioeconomics (e.g., Troy et al. 2007), property values (Kadish and Netusil 2012), vegetation preferences (e.g., Schroeder et al. 2006, Dahmus and Nelson 2014), and value orientations (Kaltenborn and Bjerke 2002).
Then, we selected two additional scales for comparison: a neighborhood scale, “within a 20-minute walk from my house” and a metro-area scale, “across the metro area.” Even in the most crowded cities, appreciation exists for features such as urban parks and greenspaces (Gidlöf-Gunnarsson and Öhrström 2007, Hoffman et al. 2012, Lo and Jim 2012), bike trails (Krizek and Johnson 2006), dispersed development (Filion et al. 1999), and walkability (Leyden 2003), which allows for maintenance of ecosystem goods and services alongside planning goals (e.g., Tratalos et al. 2007). A goal of the City of Portland and the Multnomah County Climate Action Plan (City of Portland 2009) is to establish commercial services and amenities within a 20-minute walk of all residences. This distance has been used to assess relationships between property values and green infrastructure (Mahan et al. 2000, Netusil et al. 2010). We hypothesize that convenience-related features, such as stores and services and urban parks, will more likely be important at the property- and neighborhood-level scales for Portland than for Vancouver given Portland’s policies to promote walkable neighborhoods (Table 1, H3), whereas accessible parking is more likely to be important for Vancouver (Table 1, H4).
Values are guiding ethical and moral principles for decision making and are influenced by cultural and environmental constructs (Dietz et al. 2005). We used the new ecological paradigm (NEP) framework, a common metric for assessing human understandings of and relationship with nature, to measure environmental worldviews (values) of our respondents (Table 2; Dunlap et al. 2000). Following the logic and directionality of H1, we expected that Portland respondents would be more likely to have greater NEP scores than Vancouver respondents (Table 1, H5). We used exploratory factor analysis, i.e., principle components analysis (PCA), (Sokal and Rohlf 1995, Morzillo and Mertig 2011a) for data reduction to combine statements that factored together and to construct scale scores. Cronbach’s alpha (α; Cortina 1993) provided a measure of internal reliability for each group of statements. Factor analysis produced five variables. Two variables were based on the traditional NEP (dominant social paradigm or DSP, NEP; Dunlap et al. 2000), and three were based on revealed themes of potential for environmental catastrophe (Catastrophe; Table 2), environmental dominance over human intervention (Nonintervene), and prevalence of human ingenuity over environment (Ingenuity).
Similar to values, value orientations are revealed through decision making related to codes of conduct and relationships between individuals and other people or objects (Forsyth 2006). Whereas values are based on moral principles, value orientations focus on concerns about object importance and risk (Schultz 2001, Dietz et al. 2005). Value orientations range along continua often described as biocentric-anthropocentric and protection-use (Fulton et al. 1996, Vaske et al. 2001), in which individual preferences may be reflected by perceptions (Larsen and Harland 2006) and influenced by socioeconomics (e.g., Dutcher et al. 2007). In the human dimensions of natural resources discipline, assessment of value orientations has informed the management of wildlife (e.g., Bright et al. 2000), forests (Steel et al. 1994), and landscape characteristics (Kaltenborn and Bjerke 2002). Consistent with H1 and H5, we expected that Portland respondents would exhibit fewer anthropocentric and use-based orientations than Vancouver respondents (Table 1, H6).
We assessed value orientations using three variables adapted from past research (Steel et al. 1994, Fulton et al. 1996, Bright et al. 2000, Vaske et al. 2001, Needham 2010). Two variables included subsets of 15 statements focused on general human relationships with natural resources. Using Likert format, responses to each statement were coded to indicate the level of agreement (5 = strongly agree; 4 = agree; 3 = unsure; 2 = disagree; 1 = strongly disagree); PCA and Cronbach’s alpha were applied to create scale scores. Four items factored together suggesting a human-dominated value orientation (Table 3, HumDom). Six items factored together suggesting a protectionist value orientation (Protectionist). The third variable was focused specifically on individual relationships with nature. Respondents indicated the extent that they agreed with 10 statements (Table 3, Nature), which were added together to create a scale score.
Relationships exist among socioeconomic characteristics, environmental values and orientations, and attitudes toward and behaviors related to natural resource management (e.g., Koval and Mertig 2004, Morzillo et al. 2007, Sidique et al. 2010, Morzillo and Mertig 2011a, Carter et al. 2014). Therefore, we included seven socioeconomic variables to describe respondents from our sample from both cities (Table 4).
We applied both univariate and multivariate approaches to data analysis. Univariate approaches allowed us to explore sequential differences between landscape characteristics for each city and at each scale. Multivariate techniques allowed us to explore differences between cities and scales while taking into account the entirety of survey responses. Consequently, the univariate approaches can be viewed as direct and focused questioning of differences at the individual trait level (individual landscape characteristics), and the multivariate approaches can be viewed as inquiring into the differences while considering a global view of the data. It was not our goal to present two divergent perspectives of the data, but rather to illustrate a comprehensive and holistic examination of the survey results that merge into one integrated summary of the data. All alpha values were defined as significant at the 95% confidence interval (α = 0.05).
Chi-square, ANOVA, and Pearson’s r (Sokal and Rohlf 1995) were used to compare sample means and to test bivariate relationships of socioeconomic, environmental worldview, and value orientation variables between Portland and Vancouver. Effect size (Gliner et al. 2001) was used to assess the strength of the relationships between variables, as appropriate. All univariate statistics were conducted in SPSS, unless otherwise noted.
We evaluated the importance of landscape characteristics across scales and between cities in two ways. First, nonmetric multidimensional scaling (NMDS) was used to reduce the dimensionality of all data and to explore main data patterns between the two cities. Nonmetric multidimensional scaling is a nonparametric ordination technique that measures agreement between the distance in ordination space and observed dissimilarity between survey responses (Kruskal 1964, Kruskal and Wish 1978). The agreement between ordination space and observed dissimilarity is measured by calculating stress, which is reported as a goodness of fit measure for the final NMDS. Survey responses to landscape characteristics were treated as categorical with equal distance between responses, and a Gower’s measure of distance was used to calculate distance in dissimilarity (Clarke 1993). Nonmetric multidimensional scaling and indicator analyses (Dixon 2003) were completed in R-3.0.2 using the “vegan” and “daisy” packages (R Core Team 2015).
Second, we used frequency analysis to identify the relative importance of each landscape characteristic at each scale for each city, and Chi-square analysis to test for differences between cities. Then, we applied indicator analysis (Dufrene and Legendre 1997) to calculate an overall measure of “fidelity” (affinity) for each landscape characteristic for each city; significance was tested by comparing a standard deviation weighted mean indicator value (from 1000 permutations) to the observed indicator value. Indicator species analysis was conducted in R-3.0.2 using the “labdsv” package.
The overall response rate was 18% (Portland n = 664; Vancouver n = 464). A majority of respondents were female (59%) and average (± SD) age was 53 ± 15 years. In general, Portland respondents were more likely to have children in their household, shorter residential tenure, rent, younger ages, more formal education completed, and greater incomes than Vancouver respondents (Table 4). Compared to the overall population of both cities, respondents were older, had more formal education completed, and greater household incomes (USDC 2014).
The final three-dimensional NMDS had a stress value of 0.16, which is considered to be an acceptable representation of the data (Clarke 1993). In the reduced dimensionality of our final NMDS space, there is complete mixing of Portland and Vancouver responses. Essentially, there is no shared collective pattern of important and not-important responses by residents of either city at any scale. Although the divergence between Portland and Vancouver was greatest at the metro level, relative differences in the individual questions did not result in separate clusters for each city (i.e., heterogeneity was washed out when collectively considering all positive and negative responses). Therefore, for the global multidimensional view of the data, the NMDS illustrates that the cities are indistinguishable from each other, contrasting with our hypothesis (Table 1, H1).
However, inter- and intra-city divergences were revealed for absolute differences in individual responses to discrete landscape characteristics, which varied statistically across scales for 12 of 15 landscape characteristics (Table 1, H2; Fig. 1). At the property-level scale, stores and services were considered important by the fewest Vancouver respondents, whereas streams and rivers were important to the fewest Portland respondents. At the neighborhood scale, general patterns supported our hypothesis (Table 1, H3). Large mature trees and natural stormwater management were important to the most Portland and Vancouver respondents, respectively. Conversely, plentiful accessible parking and reliable colorful flowers were least important to the Portland and Vancouver respondents, respectively. General patterns also supported our hypothesis (H3) at the metro scale, with parks with trails and natural areas identified as important to respondents in both cities.
Indicator analysis illustrated that Portland respondents showed stronger fidelity (affinity) for large mature trees, tree-lined streets, public transportation, and stores and services across all scales (Table 5). Vancouver respondents exhibited stronger affinity for plentiful accessible parking across all scales (Table 1, H4). At the property-level scale, Vancouver respondents also showed stronger affinity for vegetation that is attractive all year, well-manicured vegetation, and streams or rivers. At the neighborhood scale, Portland respondents also showed stronger affinity for urban (landscaped) parks, whereas Vancouver respondents exhibited stronger affinity for landscaping with low-cost maintenance and vegetation along streams. At the metro-area scale, Portland and Vancouver respondents also showed stronger affinity for vegetation along streams and landscaping with low-cost maintenance, respectively. The greater affinity for vegetation along streams at the neighborhood scale in Vancouver flips to Portland at the metro scale. Collectively, the magnitude of difference of affinity was generally greatest at the property-level scale.
Results of the environmental worldview analysis supported our hypothesis (Table 1, H5) that Vancouver respondents were more likely to report greater scale scores for DSP; Portland scores were more likely to be greater for NEP (Table 6). Combined scores for both cities were at the relatively low and high ends of the range for DSP and NEP, respectively. Portland respondents were more likely to report greater scale scores for Catastrophe and Nonintervene; Vancouver respondents were more likely to report greater scale scores for Ingenuity. For value orientations, HumDom values were more likely greater for Vancouver than Portland, which supports our hypothesis (H6), but Protectionist did not vary between the two cities (Table 6). Portland respondents were more likely to indicate a greater personal importance of Nature.
Decisions by urban residents have regional- and global-level impacts on ecological patterns and processes (Shochat et al. 2006, Pickett et al. 2008, Yeakley et al. 2014), including net primary productivity (Milesi et al. 2003), nutrient composition (Zhu et al. 2004), invasive species (Berland and Elliott 2014), and biodiversity (Kinzig et al. 2005, Goddard et al. 2010). These collective decisions contribute to feedbacks among other urban governance structures (Liu et al. 2007, Cook et al. 2012, Morzillo et al. 2014, Polsky et al. 2014) that influence what urban landscapes look like over time. Our hypothesis that Portland respondents would reveal more overall importance for natural resources than Vancouver respondents did not bear out at the metro scale. Rather, the two cities were quite similar. However, scaling down to the neighborhood and property levels revealed absolute affinities for particular natural and social characteristics (Table 5). To guide our discussion, we focus on three tendencies which, although unlikely mutually exclusive, may have an impact on the long-term natural resources management and the social dynamics of these cities over time.
First, preferences are segmented within the urban experience. Portland respondents illustrated affinity for proximity of urban services (e.g., public transportation, stores and services), whereas Vancouver respondents preferred amenities that require more physical space (e.g., plentiful accessible parking, streams and rivers). In Portland, county-wide transportation options include several automobile bridges over the Willamette River, limited-extent light rail, bike lanes, and commuter trains to suburbs, which together facilitate 25% of Portland workers using public, pedestrian, or bicycle transportation for work (USDC 2014). Extensive bus routes, such as those in downtown Portland also exist in Vancouver, but limited transportation infrastructure crosses the Columbia River (i.e., bus, car, Amtrak). Despite the constraints, 33% of Vancouver residents work out of state, e.g., in Oregon (USDC 2014), yet only 5% (USDC 2014) use public transportation, walk, or bicycle for transportation to work. As a result, parking is important for highly commuting-dependent Vancouver. In contrast, 78% of Portland residents work within Multnomah County (USDC 2014), and county-wide availability of public transportation may alleviate some importance of parking in Portland (Table 4). Perceptions of public transportation (e.g., Beirão and Sarsfield Cabral 2007) were beyond the scope of our data, yet compared to past research (Anable 2005) individual transportation preferences seem influenced by socioeconomics, at least for Vancouver (A.T. Morzillo, unpublished data).
Our results also suggest that Portland respondents prefer convenience across a variety of transportation modes. For instance, Portland respondent’s affinity for stores and services may be influenced by a preference for walkability (Lo 2009, Carr et al. 2011). Direct relationships between access to multiple destinations (e.g., schools, public transit, stores) and walking for transport have been reported (McCormack et al. 2008, Brown et al. 2009). Walkability has also been linked to higher home values (Cortright 2009) and lower risk of obesity (Zick et al. 2009). Despite those findings, residents of low-walkable neighborhoods have attributed greater rankings to aesthetic characteristics, such as more hills, trees, shrubs, open space, and scenic views than those in high-walkable areas (Leslie et al. 2005). Such contrast may help explain Vancouver respondents’ stronger affinity for streams and rivers and for greater importance of natural areas at the property scale (Fig. 1).
Nevertheless, affinity for nature-related characteristics existed among respondents from both cities, particularly tree-related variables for Portland respondents and vegetation along streams for Vancouver respondents. Benefits of urban trees and vegetation include reducing heat island effects (Grimm et al. 2008), stormwater management (Yeakley 2014), stress reduction (Carrus et al. 2015, Taylor et al. 2015), familiarity (Henwood and Pidgeon 2001), reduced crime rates (Kondo et al. 2015), carbon sequestration and pollutant reduction (McPhearson et al. 2013), and oxygen provision (Camacho-Cervantes et al. 2014). Relationships with particular socioeconomic conditions have been noted (Landry and Chakraborty 2009, Conway et al. 2011). Amid the urban experience, greenery as small as individual trees may provide a connection with nature for Portland residents, who are generally further from streams. In addition, the younger age and greater likelihood of having children for Portland respondents may suggest the role of urban parks for daily connection with nature (e.g., Payne et al. 2002, Balram and Dragićević 2005) and as social outlets for families and residents with dogs (e.g., Germann-Chiari and Seeland 2004, Grahn and Stigsdotter 2010, Schipperijn et al. 2010). Thus, preference for at least some urban nature exists along with willingness to forego proximity to natural areas for the convenience of transportation and consumer services.
Second, differences between the two cities also may be influenced by economics. Economic theory posits that, under certain conditions, citizens “vote with their feet” and move to communities that most closely align with their preferences for land-use policies, tax policies, and publicly provided goods (Tiebout 1956). Hence, Portland respondents’ strong and consistent affinities for public transportation and stores and services across scales could be an unintended outcome of Oregon’s more aggressive approach to land-use planning (Kline et al. 2014). Differences in tax policies between the two states (Philen 2014, Oregon Legislative Revenue Office 2015) may also contribute to Vancouver respondents’ greater affinity for parking and less affinity for nearby stores and services (Table 5). Washington has no income tax, but it has a sales tax; Oregon has no sales tax, but relies heavily on income tax revenue. This diversity may lead to tax avoidance whereby Vancouver residents shop in Oregon to minimize sales tax, yet live in Washington to minimize income tax. However, testing this speculation is beyond the scope of our data.
Economic theory also implies that tax policies and amenities should be capitalized into the sale price of residential properties (Freeman 2003). Research applying the hedonic price technique has found that property sale prices in Portland are influenced by open space proximity (Lutzenhiser and Netusil 2001), type and proximity of wetlands (Mahan et al. 2000), walkability (Cortright 2009), and street trees (Donovan and Butry 2010). Therefore, from our results (Fig. 1), we hypothesized that a hedonic study using property sale data from Portland and Vancouver would find a higher marginal willingness to pay in Vancouver for well-manicured vegetation and vegetation along streams, and a higher marginal willingness to pay in Portland for the presence of large mature trees, tree-lined streets, public transportation, and stores and services.
Finally, personal relationship with the environment may contribute to the importance of landscape characteristics. Our results support our hypotheses that Portland respondents are more likely to have greater NEP scores than Vancouver respondents, and that Vancouver respondents exhibit more anthropocentric and use-based orientations than Portland respondents. Given these differences, we speculate that affinity for public transportation and proximity to stores and services among Portland respondents may be associated with a desire to be environmentally altruistic; yet, the literature is mixed in supporting this assertion. For example, Bopp et al. (2011) reported an inverse relationship between commuting time and average eco-friendly attitudes among young adults. However, public transportation usage and other environmentally related behaviors have been linked to not only personal environmental norms, but also emotional characteristics (Bamberg et al. 2007, Carrus et al. 2008). Specific to our objective, public transportation may support a theme of cognitive based, self-sorting of individuals between cities (Bamberg et al. 2007). Relatively greater scores for Nonintervene, Ingenuity, and HumDom among Vancouver respondents could reflect preferences for inventiveness versus inevitability (see Bamberg et al. 2007 for an example of potential segmentation based on industrial-postindustrial characteristics) and represent a combination of social relics and driving forces behind the different land-use planning models of the two states. Directly testing this assertion would require longitudinal analysis. Nevertheless, others have noted the role of time lags and land legacy in both inherited versus contemporary observed landscape characteristics (Boone et al. 2010).
A global view of the data provides further insight into metro-area dynamics, and similarities and interdependencies of the two cities as an integrated multiscalar system (Ostrom 2010, Liu et al. 2013). Commute patterns (USDC 2014) illustrate strong functional linkages between the two cities. Elsewhere in this study, data suggest that respondents may view particular environmental characteristics (e.g., water quality) of the “other” city as different than their own (A.T. Morzillo, unpublished data). However, influences of shared public dialogue and communication outlets (e.g., news media such as TV stations), strong interactions between professional groups (e.g., natural-resource managers, urban planners, and foresters), and geographic similarities may be more important than location of the cities in two different states (Sterrett et al. 2015).
Although the land-use planning histories of Oregon (i.e., safeguard economic production) and Washington (i.e., protect open space) differ in historical motivation, our results indicate some consistencies in resident perceptions between the two cities. Preliminary results of ongoing analysis suggest “Nature” (Table 3) to be the most consistent variable to influence the importance of all 15 landscape characteristics for both cities (A.T. Morzillo, unpublished data). Personal relationship with the environment is a consistent driver of support for decision making related to natural resource conservation (e.g., Morzillo and Mertig 2011b). However, individual preferences may be reflected in object-based attitudes (e.g., Morzillo and Mertig 2011b, Camacho-Cervantes et al. 2014, Belaire et al. 2016), reflect discourse among human perceptions of nature (Steinberg et al. 2015), and the influence of socioeconomics. For example, urban versus rural residence and more formal education are often correlated with variation in environmental concern (e.g., Van Liere and Dunlap 1980, Hayes 1989, Arcury and Christianson 1993, Dietz et al. 1998, Berenguer et al. 2005, Freudenburg 1991, Morzillo and Mertig 2011a, b, Newman and Fernandes 2016). In our case, homogeneity of our respondents as geographically “urban” (i.e., within the metropolitan area) may have influenced environmental predictors, as supported by generally high scale scores for NEP and equally for Protectionist. Although it is difficult to measure (Hawcroft and Milfont 2010) and directly compare our results to other locations, trends in NEP have increased over time in tandem with social environmental movements and rural-to-urban human population shifts (Dunlap et al. 2000, Inglehart and Baker 2000). In addition, more than 30% of those in the Portland-Vancouver-Hillboro consolidated metropolitan statistical area (2010 U.S. Census; USDC 2014) and our respondents (Table 4) were college graduates, which is greater than the population at large (USDC 2014) and disallows broader regional inferences. We also note overall demographic differences between our respondents and census data (USDC 2014) which, regardless of nonresponse follow-up, reinforce limitations in generalizing our results to the whole metropolitan area based on intent and use of our sampling strategy and data collection (Dillman et al. 2009). It is clear that there are multiple factors affecting decision making. Therefore, it is unlikely that uniform policies that assume homogeneity among preferences for urban landscape characteristics are appropriate.
Urban landscapes are the result of complex decisions made over multiple spatial and temporal scales. Although our data seemed homogeneous at the broadest scope, we detected nuances at multiple scales of analysis with the greatest differences generally at the property-level scale. The cumulative effect of property-level decisions affects landscape characteristics at coarser scales. Governance can overcome collective action problems that arise when individual decisions result in outcomes that are not optimal when viewed at a larger scale. In our case, historical and existing land-use policies may be contributing to self-fulfilling processes of actual development patterns over time, particularly in the case of Oregon. However, these patterns only occur at certain scales and among many competing factors. Inmigrants seeking regional geographic amenities may not differentiate between Portland and Vancouver. However, each city has its own social culture that takes time to develop, maintain, and further evolve depending on what trade-offs communities are willing to make. Further exploration of such relationships will likely support a broader story about how such patterns contribute to feedback loops over time.
The Portland-Vancouver ULTRA-Ex efforts include many project personnel from Portland State University, Washington State University - Vancouver, Oregon State University, Reed College, and the US Forest Service Pacific Northwest Research Station, with input from several land management agencies. Thank you to the Portland-Vancouver ULTRA-Ex project team for inspiring this research based on a friendly project meeting quarrel about which of the two cities is better. We individually thank K. Heavener, H. Chang, V. Shandas, J. Kline, S. Bollens, G. Rollwagen-Bollens, P. Thiers, S. Gordon, M. Dresner, A. Phillip, B. Pratt, T. Gibson, M. Smith, J. Bevis, M. Atkinson, A. Mertig, D. Kloster, L. Keener-Eck, three anonymous reviewers, and all Portland-Vancouver residents who completed the survey. This work was supported by the National Science Foundation Grants #0948983, #0948826, and #0949042, Oregon State University General Research Fund, Portland State University, and Reed College. Use of human subjects was approved by Oregon State University (IRB #5022), Portland State University (#111816), Washington State University (#12019), Reed College (#Netusil 2012), and University of Connecticut (#H14-194). This paper has not been subjected to formal US EPA review. Therefore, it does not necessarily reflect the views of the Agency. Mention of trade names or commercial products does not constitute endorsement or recommendation for use by the US Government. This is contribution number ORD-012384 of the Atlantic Ecology Division, Office of Research and Development, National Health and Environmental Effects Research Laboratory.
Ahern, J. 2013. Urban landscape sustainability and resilience: the promise and challenges of integrating ecology with urban planning and design. Landscape Ecology 28:1203-1212. http://dx.doi.org/10.1007/s10980-012-9799-z
Alberti, M., J. M. Marzluff, E. Shulenberger, G. Bradley, C. Ryan, and C. Zumbrunnen. 2003. Integrating humans into ecology: opportunities and challenges for studying urban ecosystems. Bioscience 53:1169-1179. http://dx.doi.org/10.1641/0006-3568(2003)053[1169:IHIEOA]2.0.CO;2
Anable, J. 2005. ‘Complacent car addicts’ or ‘aspiring environmentalists’? Identifying travel behavior segments using attitude theory. Transport Policy 12:65-78. http://dx.doi.org/10.1016/j.tranpol.2004.11.004
Ando, A. W., and L. P. C. Freitas. 2011. Environmental feedback and consumer demand for green technology: the case of Chicago rain barrels. Water Resources Research 47(12):W12501. http://dx.doi.org/10.1029/2011WR011070
Arcury, T. A., and E. H. Christianson. 1993. Rural-urban differences in environmental knowledge and actions. Journal of Environmental Education 25:19-25. http://dx.doi.org/10.1080/00958964.1993.9941940
Balram, S., and S. Dragićević. 2005. Attitudes toward urban green spaces: integrating questionnaire survey and collaborative GIS techniques to improve attitude measurements. Landscape and Urban Planning 71:147-162. http://dx.doi.org/10.1016/S0169-2046(04)00052-0
Bamberg, S., M. Hunecke, and A. Blöbaum. 2007. Social context, personal norms, and the use of public transportation: two field studies. Journal of Environmental Psychology 27:190-203. http://dx.doi.org/10.1016/j.jenvp.2007.04.001
Beirão, G., and J. A. Sarsfield Cabral. 2007. Understanding attitudes toward public transport and private car: a qualitative study. Transport Policy 14:478-489. http://dx.doi.org/10.1016/j.tranpol.2007.04.009
Belaire, J. A., L. M. Westphal, and E. S. Minor. 2016. Different social drivers, including perceptions of urban wildlife, explain the ecological resources in residential landscapes. Landscape Ecology 31:401-413. http://dx.doi.org/10.1007/s10980-015-0256-7
Belaire, J. A., C. J. Whelan, and E. S. Minor. 2014. Having our yards and sharing them too: the collective effects of yards on native bird species in an urban landscape. Ecological Applications 24:2132-2143. http://dx.doi.org/10.1890/13-2259.1
Berenguer, J., J. A. Corraliza, and R. Martín. 2005. Rural-urban differences in environmental concern, attitudes, and actions. European Journal of Psychological Assessment 21:128-138. http://dx.doi.org/10.1027/1015-57188.8.131.52
Berland, A., and G. P. Elliott. 2014. Unexpected connections between residential urban forest diversity and vulnerability to two invasive beetles. Landscape Ecology 29:141-152. http://dx.doi.org/10.1007/s10980-013-9953-2
Boone, C. G., M. L. Cadenasso, J. M. Grove, K. Schwarz, and G. L. Buckley. 2010. Landscape, vegetation characteristics, and group identity in an urban and suburban watershed: why the 60s matter. Urban Ecosystems 13:255-271. http://dx.doi.org/10.1007/s11252-009-0118-7
Bopp, M., A. T. Kaczynski, and P. Wittman. 2011. The relationship of eco-friendly attitudes with walking and biking to work. Journal of Public Health Management and Practice 17:E9-E17. http://dx.doi.org/10.1097/phh.0b013e31821138de
Bright, A. D., M. J. Manfredo, and D. Fulton. 2000. Segmenting the public: an application of value orientations to wildlife planning in Colorado. Wildlife Society Bulletin 28:218-226.
Brown, B. B., I. Yamada, K. R. Smith, C. D. Zick, L. Kowaleski-Jones, and J. X. Fan. 2009. Mixed land use and walkability: variations in land use measures and relationships with BMI, overweight, and obesity. Health and Place 15:1130-1141. http://dx.doi.org/10.1016/j.healthplace.2009.06.008
Camacho-Cervantes, M., J. E. Schondube, A. Castillo, and I. MacGregor-Fors. 2014. How do people perceive urban trees? Assessing likes and dislikes in relation to the trees of a city. Urban Ecosystems 17:761-773. http://dx.doi.org/10.1007/s11252-014-0343-6
Carr, L. J., S. I. Dunsiger, and B. H. Marcus. 2011. Validation of walk score for estimating access to walkable amenities. British Journal of Sports Medicine 45:1144-1148. http://dx.doi.org/10.1136/bjsm.2009.069609
Carrus, G., P. Passafaro, and M. Bonnes. 2008. Emotions, habits, and rational choices in ecological behaviours: the case of recycling and use of public transportation. Journal of Environmental Psychology 28:51-62. http://dx.doi.org/10.1016/j.jenvp.2007.09.003
Carrus, G., M. Scopelliti, R. Lafortezza, G. Colangelo, F. Ferrini, F. Salbitano, M. Agrimi, L. Portoghesi, P. Semenzato, and G. Sanesi. 2015. Go greener, feel better? The positive effects of biodiversity on the well-being of individuals visiting urban and peri-urban green areas. Landscape and Urban Planning 134:221-228. http://dx.doi.org/10.1016/j.landurbplan.2014.10.022
Carter, N. H., S. J. Riley, A. Shortridge, B. K. Shrestha, and J. Liu. 2014. Spatial assessment of attitudes toward tigers in Nepal. AMBIO 43:125-137. http://dx.doi.org/10.1007/s13280-013-0421-7
Champ, P. A., K. J. Boyle, and T. C. Brown, editors. 2003. A primer on nonmarket valuation. Springer, Norwell, Maine, USA. http://dx.doi.org/10.1007/978-94-007-0826-6
Chang, H., P. Thiers, N. R. Netusil, J. A. Yeakley, G. Rollwagen-Bollens, S. M. Bollens, and S. Singh. 2014. Relationships between environmental governance and water quality in a growing metropolitan area of the Pacific Northwest, USA. Hydrology and Earth System Sciences 18:1383-1395. http://dx.doi.org/10.5194/hess-18-1383-2014
Chowdhury, R. R., K. Larson, M. Grove, C. Polsky, E. Cook, J. Onsted, and L. Ogden. 2011. A multi-scalar approach to theorizing socio-ecological dynamics of urban residential landscapes. Cities and the Environment 4(1):6. http://dx.doi.org/10.15365/cate.4162011
City of Portland. 2009. City of Portland and Multnomah County climate action plan. 2009. City of Portland Bureau of Planning and Sustainability, Portland, Oregon, USA. [online] https://www.portlandoregon.gov/bps/49989
Clarke, K. R. 1993. Non-parametric multivariate analyses of changes in community structure. Australian Journal of Ecology 18:117-143. http://dx.doi.org/10.1111/j.1442-9993.1993.tb00438.x
Collins, S. L., S. R. Carpenter, S. M. Swinton, D. E. Orenstein, D. L. Childers, T. L. Gragson, N. B. Grimm, J. M. Grove, S. L. Harlan, J. P. Kaye, A. K. Knapp, G. P. Kofinas, J. J. Magnuson, W .H. McDowell, J. M. Melack, L. A. Ogden, G. P. Robertson, M. D. Smith, and A. C. Whitmer. 2011. An integrated conceptual framework for long-term social-ecological research. Frontiers in Ecology and the Environment 9:351-357. http://dx.doi.org/10.1890/100068
Collins, J., A. Kinzig, N. Grimm, W. Fagan, D. Hope, J. Wu, and E. Borer. 2000. A new urban ecology: modeling human communities as integral parts of ecosystems poses special problems for the development and testing of ecological theory. American Scientist 88:416-425. http://dx.doi.org/10.1511/2000.5.416
Conway, T. M., T. Shakeel, and J. Atallah. 2011. Community groups and urban forestry activity: drivers of uneven canopy cover? Landscape and Urban Planning 101:321-329. http://dx.doi.org/10.1016/j.landurbplan.2011.02.037
Cook, E. M., S. J. Hall, and K. L. Larson. 2012. Residential landscapes as social-ecological systems: a synthesis of multi-scalar interactions between people and their home environment. Urban Ecosystems 15:19-52. http://dx.doi.org/10.1007/s11252-011-0197-0
Cortina, J. M. 1993. What is coefficient alpha? An examination of theory and applications. Journal of Applied Psychology 78:98-104. http://dx.doi.org/10.1037/0021-9010.78.1.98
Cortright, J. 2009. Walking the walk: how walkability raises home values in U.S. cities. 2009. Impresa, Portland, Oregon, USA. [online] URL: http://blog.walkscore.com/wp-content/uploads/2009/08/WalkingTheWalk_CEOsforCities.pdf
Dahmus, M. E., and K. C. Nelson. 2014. Yard stories: examining residents’ conceptions of their yards as part of the urban ecosystem in Minnesota. Urban Ecosystems 17:173-194. http://dx.doi.org/10.1007/s11252-013-0306-3
Dietz, T., A. Fitzgerald, and R. Shwom. 2005. Environmental values. Annual Review of Environment and Resources 30:335-372. http://dx.doi.org/10.1146/annurev.energy.30.050504.144444
Dietz, T., P. C. Stern, and G. A. Guagnano. 1998. Social structural and social psychological bases of environmental concern. Environment and Behavior 30:450-471. http://dx.doi.org/10.1177/001391659803000402
Dillman, D. A, J. D. Smyth, and L. M. Christian. 2009. Internet, mail, and mixed-mode surveys: the tailored design method. Third edition. John Wiley and Sons, Hoboken, New Jersey, USA.
Dixon, P. 2003. VEGAN, a package of R functions for community ecology. Journal of Vegetation Science 14:927-930. http://dx.doi.org/10.1111/j.1654-1103.2003.tb02228.x
Donovan, G. H., and D. T. Butry. 2010. Trees in the city: valuing street trees in Portland, Oregon. Landscape and Urban Planning 94:77-83. http://dx.doi.org/10.1016/j.landurbplan.2009.07.019
Dufrene, M., and P. Legendre. 1997. Species assemblages and indicator species: the need for a flexible asymmetrical approach. Ecological Monograph 67:345-366. http://dx.doi.org/10.2307/2963459
Duh, J.-D., V. Shandas, H. Chang, and L. A. George. 2008. Rates of urbanisation and the resiliency of air and water quality. Science of the Total Environment 400:238-256. http://dx.doi.org/10.1016/j.scitotenv.2008.05.002
Dunlap, R. E., K. D. Van Liere, A. G. Mertig, and R. E. Jones. 2000. New trends in measuring environmental attitudes: measuring endorsement of the new ecological paradigm: a revised NEP scale. Journal of Social Issues 56:425-442. http://dx.doi.org/10.1111/0022-4537.00176
Dutcher, D. D., J. C. Finley, A. E. Luloff, and J. B. Johnson. 2007. Connectivity with nature as a measure of environmental values. Environment and Behavior 39:474-493. http://dx.doi.org/10.1177/0013916506298794
Elmqvist, T., M. Fragkias, J. Goodness, B. Günerlap, P. J. Marcotullio, R. I. McDonald, S. Parnell, M. Schewenius, M. Sendstad, K. C. Seto, and C. Wilkinson, editors. 2013. Urbanization, biodiversity, and ecosystem services: challenges and opportunities. Springer, New York, New York, USA. http://dx.doi.org/10.1007/978-94-007-7088-1
Everett, G., J. Lamond, A. T. Morzillo, F. K. S. Chan, and A. M. Matsler. 2016. Sustainable drainage systems: helping people live with water. Water Management 169:94-104. http://dx.doi.org/10.1680/wama.14.00076
Filion, P., T. Buntin, and K. Warriner. 1999. The entrenchment of urban dispersion: residential preferences and location patterns in the dispersed city. Urban Studies 36:1317-1347. http://dx.doi.org/10.1080/0042098993015
Forsyth, D. R. 2006. Group dynamics. Fourth edition. Brooks/Cole, Pacific Grove, California, USA.
Freeman, A. M., III. 2003. The measurement of environmental and resource values: theory and methods. Second edition. Resources for the Future, Washington, D.C., USA.
Freudenburg, W. R. 1991. Rural-urban differences in environmental concern: a closer look. Sociological Inquiry 61:167-198. http://dx.doi.org/10.1111/j.1475-682X.1991.tb00274.x
Fulton, D. C., M. J. Manfredo, and J. Lipscomb. 1996. Wildlife value orientations: a conceptual and measurement approach. Human Dimensions of Wildlife 1:24-47. http://dx.doi.org/10.1080/10871209609359060
Geoghegan, J. 2002. The value of open spaces in residential land use. Land Use Policy 19:91-98. http://dx.doi.org/10.1016/S0264-8377(01)00040-0
Germann-Chiari, C., and K. Seeland. 2004. Are urban green spaces optimally distributed to act as places for social integration? Results of a geographical information system (GIS) approach for urban forestry research. Forest Policy and Economics 6:3-13. http://dx.doi.org/10.1016/S1389-9341(02)00067-9
Gidlüf-Gunnarsson, A., and E. Öhrstrüm. 2007. Noise and well-being in urban residential environments: the potential role of perceived availability to nearby green areas. Landscape and Urban Planning 83:115-126. http://dx.doi.org/10.1016/j.landurbplan.2007.03.003
Gliner J. A., J. J. Vaske, and G. A. Morgan. 2001. Null hypothesis significance testing: effect size matters. Human Dimensions of Wildlife 6:291-301. http://dx.doi.org/10.1080/108712001753473966
Goddard, M. A., A. J. Dougill, and T. G. Benton. 2010. Scaling up from gardens: biodiversity conservation in urban environments. Trends in Ecology and Evolution 25:90-98. http://dx.doi.org/10.1016/j.tree.2009.07.016
Grahn, P., and U. K. Stigsdotter. 2010. The relation between perceived sensory dimensions or urban green space and stress restoration. Landscape and Urban Planning 94:264-275. http://dx.doi.org/10.1016/j.landurbplan.2009.10.012
Greenbiz. 2008. Portland named America’s greenest city. [online] URL: https://www.greenbiz.com/news/2008/02/19/portland-named-americas-greenest-city
Grimm, N. B., S. H. Faeth, N. E. Golubiewski, C. L. Redman, J. Wu, X. Bai, and J. M. Briggs. 2008. Global change and the ecology of cities. Science 319:756-760. http://dx.doi.org/10.1126/science.1150195
Hawcroft, L. J., and T. L. Milfont. 2010. The use (and abuse) of the new environmental paradigm scale over the last 30 years: a meta-analysis. Journal of Environmental Psychology 30:143-158. http://dx.doi.org/10.1016/j.jenvp.2009.10.003
Hayes, S. P. 1989. Beauty, health, and permanence. Cambridge University Press, Cambridge, UK. http://dx.doi.org/10.1017/cbo9780511664106
Henwood, K., and N. Pidgeon. 2001 Talk about woods and trees: threat of urbanization, stability, and biodiversity. Journal of Environmental Psychology 21:125-147. http://dx.doi.org/10.1006/jevp.2000.0196
Hoffman, M., J. R. Westermann, I. Kowarik, and E. van der Meer. 2012. Perceptions of parks and urban derelict land by landscape planners and residents. Urban Forestry and Urban Greening 11:303-312. http://dx.doi.org/10.1016/j.ufug.2012.04.001
Inglehart, R., and W. E. Baker. 2000. Modernization, cultural change, and the persistence of traditional values. American Sociological Review 65:19-51. http://dx.doi.org/10.2307/2657288
Kadish, J., and N. R. Netusil. 2012. Valuing vegetation in an urban watershed. Landscape and Urban Planning 104:59-65. http://dx.doi.org/10.1016/j.landurbplan.2011.09.004
Kaltenborn, B. P., and T. Bjerke. 2002. Associations between environmental value orientations and landscape preferences. Landscape and Urban Planning 59:1-11. http://dx.doi.org/10.1016/S0169-2046(01)00243-2
Kinzig, A. P., P. Warren, C. Martin, D. Hope, and M. Katti. 2005. The effects of human socioeconomic status and cultural characteristics on urban patterns of biodiversity. Ecology and Society 10:(1)23. [online] URL: http://www.ecologyandsociety.org/vol10/iss1/art23/
Kline, J. D., P. Thiers, C. P. Ozawa, J. A. Yeakley, and S. N. Gordon. 2014. How well has land-use planning worked under different governance regimes? A case study in the Portland, OR-Vancouver, WA metropolitan area, USA. Landscape and Urban Planning 131:51-63. http://dx.doi.org/10.1016/j.landurbplan.2014.07.013
Kondo, M. C., S. C. Low, J. Henning, and C. C. Branas. 2015. The impact of green stormwater infrastructure installation on surrounding health and safety. American Journal of Public Health 105:e114-e121. http://dx.doi.org/10.2105/ajph.2014.302314
Koval, M. H., and A. G. Mertig. 2004. Attitudes of the Michigan public and wildlife agency personnel toward lethal wildlife management. Wildlife Society Bulletin 32:232-243. http://dx.doi.org/10.2193/0091-7648(2004)32[232:AOTMPA]2.0.CO;2
Krizek, K. J., and P. J. Johnson 2006. Proximity to trails and retail: effects on urban cycling and walking. Journal of the American Planning Association 72:33-42. http://dx.doi.org/10.1080/01944360608976722
Kruskal, J. B. 1964. Nonmetric multidimensional scaling: a numerical method. Psychometrika 29:115-129. http://dx.doi.org/10.1007/BF02289694
Kruskal, J. B., and M. Wish. 1978. Multidimensional scaling. Sage, Thousand Oaks, California, USA. http://dx.doi.org/10.4135/9781412985130
Landry, S. M., and J. Chakraborty. 2009. Street trees and equity: evaluating the spatial distribution of an urban amenity. Environment and Planning A 41:2651-2670. http://dx.doi.org/10.1068/a41236
Larsen, L., and S. L. Harlan. 2006. Desert dreamscapes: residential landscape preference and behavior. Landscape and Urban Planning 78:85-100. http://dx.doi.org/10.1016/j.landurbplan.2005.06.002
Leslie, E., B. Saelens, L. Frank, N. Owen, A. Bauman, N. Coffee, and G. Hugo. 2005. Residents’ perceptions of walkability attributes in objectively different neighborhoods: a pilot study. Health and Place 11:227-236. http://dx.doi.org/10.1016/j.healthplace.2004.05.005
Lettman, G., K. Daniels, and T. Trahimovic. 2014. Protecting working farm and forest landscapes: how do Oregon and Washington compare? Pages 42-53 in J. Sterrett, C. Ozawa, D. Ryan, E. Seltzer, and J. Whittington, editors. Planning the Pacific Northwest APA Press, Chicago, Illinois, USA.
Leyden, K. M. 2003. Social capital and the built environment: the importance of walkable neighborhoods. American Journal of Public Health 93:1546-1551. http://dx.doi.org/10.2105/AJPH.93.9.1546
Liu, J., T. Dietz, S. R. Carpenter, M. Alberti, C. Folke, E. Moran, A. N. Pell, P. Deadman, T. Kratz, J. Lubchenco, E. Ostrom, Z. Ouyang, W. Provencher, C. L. Redman, S. H. Schneider, and W. W. Taylor. 2007. Complexity of coupled human and natural systems. Science 317:1513-1516. http://dx.doi.org/10.1126/science.1144004
Liu, J., V. Hull, M. Batistella, R. DeFries, T. Dietz, F. Fu, T. W. Hertel, R. C. Izaurralde, E. F. Lambin, S. Li, L. A. Martinelli, W. J. McConnell, E. F. Moran, R. Naylor, Z. Ouyang, K. R. Polenske, A. Reenberg, G. de Miranda Rocha, C. S. Simmons, P. H. Verburg, P. M. Vitousek, F. Zhang, and C. Zhu. 2013. Framing sustainability in a telecoupled world. Ecology and Society 18(2):26. http://dx.doi.org/10.5751/es-05873-180226
Lo, Ria Hutabarat. 2009. Walkability: what is it? Journal of Urbanism 2:145-166. http://dx.doi.org/10.1080/17549170903092867
Lo, A. Y. H., and C. Y. Jim. 2012. Citizen attitude and expectation towards greenspace provision in compact urban milieu. Land Use Policy 29:577-586. http://dx.doi.org/10.1016/j.landusepol.2011.09.011
Londoño Cadavid, C. 2013. Using choice experiments to value preferences over stormwater management. Dissertation. University of Illinois at Urbana-Champaign, Urbana, Illinois, USA. [online] URL: https://www.ideals.illinois.edu/bitstream/handle/2142/45536/Catalina_Londono%20Cadavid.pdf?sequence=1
Lutzenhiser, M., and N. R. Netusil. 2001. The effect of open spaces on a home’s sale price. Contemporary Economic Policy 19:291-298. http://dx.doi.org/10.1093/cep/19.3.291
Mahan, B. L., S. Polasky, and R. M. Adams. 2000. Valuing urban wetlands: a property price approach. Land Economics 76:100-113. http://dx.doi.org/10.2307/3147260
Martin, C. A., K. A. Peterson, and L. B. Stabler. 2003. Residential landscaping in Phoenix, Arizona, U.S.: practices and preferences relative to covenants, codes, and restrictions. Journal of Arboriculture 29:9-17.
McCormack, G. R., B. Giles-Corti, and M. Bulsara. 2008. The relationship between destination proximity, destination mix and physical activity barriers. Preventive Medicine 46:33-40. http://dx.doi.org/10.1016/j.ypmed.2007.01.013
McDonnell, M. J., and S. T. A. Pickett. 1997. Humans as components of ecosystems: the ecology of subtle human effects and populated areas. Springer-Verlag, New York, New York, USA. http://dx.doi.org/10.1007/978-1-4612-0905-8
McPhearson, T., P. Kremer, and Z. A. Hamstead. 2013. Mapping ecosystem services in New York City: applying a social-ecological approach in urban vacant land. Ecosystem Services 5:11-26. http://dx.doi.org/10.1016/j.ecoser.2013.06.005
Milesi, C., C. D. Elvidge, R. R. Nemani, and S. W. Running. 2003. Assessing the impact of urban land development on net primary productivity in the southeastern United States. Remote Sensing of Environment 86:401-410. http://dx.doi.org/10.1016/S0034-4257(03)00081-6
Morzillo, A. T., K. M. deBeurs, and C. J. Martin-Mikle. 2014. A conceptual framework to evaluate human-wildlife interactions within coupled human and natural systems. Ecology and Society 19(3):44. http://dx.doi.org/10.5751/es-06883-190344
Morzillo, A. T., and A. G. Mertig. 2011a. Urban resident attitudes toward rodents, rodent control products, and environmental effects. Urban Ecosystems 14:243-260. http://dx.doi.org/10.1007/s11252-010-0152-5
Morzillo, A. T., and A. G. Mertig. 2011b. Linking human behavior to environmental effects using a case study of urban rodent control. International Journal of Environmental Studies 68:107-123. http://dx.doi.org/10.1080/00207233.2010.527462
Morzillo, A. T., A. G. Mertig, N. Garner, and J. Liu. 2007. Resident attitudes toward black bears and a proposed recovery in East Texas. Human Dimensions of Wildlife 12:417-428. http://dx.doi.org/10.1080/10871200701670110
Morzillo, A. T., and M. D. Schwartz. 2011. Landscape characteristics affect animal control by urban residents. Ecosphere 2:1-16. http://dx.doi.org/10.1890/ES11-00120.1
Muller, P. O. 1982. Everyday life in suburbia: a review of changing social and economic forces that shape daily rhythms within the outer city. American Quarterly 34:262-277. http://dx.doi.org/10.2307/2712778
Needham, M. D. 2010. Value orientations toward coral reefs in recreation and tourism settings: a conceptual and measurement approach. Journal of Sustainable Tourism 18:757-772. http://dx.doi.org/10.1080/09669581003690486
Netusil, N. R., S. Chattopadhyay, and K. F. Kovacs. 2010. Estimating the demand for tree canopy: a second-stage hedonic price analysis in Portland, Oregon. Land Economics 86:281-293. http://dx.doi.org/10.3368/le.86.2.281
Netusil, N. R., M. Kincaid, and H. Chang. 2014. Valuing water quality in urban watersheds: a comparative analysis of Johnson Creek, Oregon, and Burnt Bridge Creek, Washington. Water Resources Research 50:4254-4268. http://dx.doi.org/10.1002/2013WR014546
Newman, T. P., and R. Fernandes. 2016. A re-assessment of factors associated with environmental concern and behavior using the 2010 general social survey. Environmental Education Research 22:153-175. http://dx.doi.org/10.1080/13504622.2014.999227
Oregon Department of Land Conservation and Development. 2006. Oregon’s statewide planning goals and guidelines, goal 14: urbanization (OAR 660-015-0000(14). Oregon Department of Land Conservation and Development, Salem, Oregon, USA. [online] URL: http://www.oregon.gov/LCD/Pages/goals.aspx
Oregon Legislative Revenue Office. 2015. 2015 Oregon public finance: basic facts. State of Oregon Legislative Revenue Office, Salem, Oregon, USA. [online] URL: https://www.oregonlegislature.gov/lro/Documents/Basic%20Facts%202015.pdf
Ostrom, E. 2010. Beyond markets and states: polycentric governance of complex economic systems. American Economic Review 100:641-672. http://dx.doi.org/10.1257/aer.100.3.641
Payne, L. L., A. J. Mowen, and E. Orsega-Smith. 2002. An examination of park preferences and behaviors among urban residents: the role of residential location, race, and age. Leisure Sciences 24:181-198. http://dx.doi.org/10.1080/01490400252900149
Philen, R. 2014. Comparative state and local taxes 2012. Washington State Department of Revenue, Olympia, Washington, USA. [online] URL: http://dor.wa.gov/content/aboutus/statisticsandreports/stats_complist.aspx
Pickett, S. T. A., and M. J. McDonnell. 1993. Humans as components of ecosystems: a synthesis. 1997. Pages 310-316 in M. J. McDonnell and S. T. A. Pickett, editors. Humans as components of ecosystems: the ecology of subtle human effects and populated areas. Springer-Verlag, New York, New York, USA. http://dx.doi.org/10.1007/978-1-4612-0905-8_24
Pickett, S. T. A., M. L. Cadenasso, J. M Grove, P. M. Groffman, L. E. Band, C. G. Boone, W. R. Burch, Jr., C. S. B. Grimmond, J. Hom, J. C. Jenkins, N. L. Law, C. H. Nilon, R. V. Pouyat, K. Szlavecz, P. S. Warren, and M. A. Wilson. 2008. Beyond urban legends: an emerging framework of urban ecology, as illustrated by the Baltimore ecosystem study. Bioscience 58:139-150. http://dx.doi.org/10.1641/B580208
Pickett, S. T. A., M. L. Cadenasso, J. M. Grove, C. H. Nilon, R. V. Pouyat, W. C. Zipperer, and R. Costanza. 2001. Urban ecological systems: linking terrestrial ecological, physical, and socioeconomic components of metropolitan areas. Annual Review of Ecology, Evolution, and Systematics 32:127-157. http://dx.doi.org/10.1146/annurev.ecolsys.32.081501.114012
Polsky, C., J. M. Grove, C. Knudson, P. M. Groffman, N. Bettez, J. Cavender-Bares, S. J. Hall, J. B. Heffernan., S. E. Hobbie, K. L. Larson, J. L. Morse, C. Neill, K. C. Nelson, L. A. Ogden, J. O’Neil-Dunne, D. E. Pataki, R. R. Chowdhury, and M. K. Steele. 2014. Assessing the homogenization of urban land management with an application to US residential lawn care. Proceedings of the National Academy of Sciences 111:4432-4437. http://dx.doi.org/10.1073/pnas.1323995111
R Core Team. 2015. R: a language and environment for statistical computing. R Foundation for Statistical Computing, Vienna, Austria. [online] URL: http://www.R-project.org/
Schipperijn, J., O. Ekholm, U. K. Stigsdotter, M. Toftager, P. Bentsen, F. Kamper-Jørgensen, and T. B. Randrup. 2010. Factors influencing the use of green space: results from a Danish national representative survey. Landscape and Urban Planning 95:130-137. http://dx.doi.org/10.1016/j.landurbplan.2009.12.010
Schroeder, H., J. Flannigan, and R. Coles. 2006. Residents’ attitudes toward street trees in the UK and U.S. communities. 2006. Arboriculture and Urban Forestry 32:236-246. [online] URL: http://conservation.ufl.edu/urbanforestry/Resources/PDF%20downloads/Schroeder%20_2006.pdf
Schultz, P. W. 2001. The structure of environmental concern: concern for self, other people, and the biosphere. Journal of Environmental Psychology 21:327-339. http://dx.doi.org/10.1006/jevp.2001.0227
Seto, K. C., M. Fragkias, B. Güneralp, and M. K. Reilly. 2011. A meta-analysis of global urban land expansion. PLoS ONE 6:e23777. http://dx.doi.org/10.1371/journal.pone.0023777
Seto, K. C., B. Güneralp, and L. Hutyra. 2012. Global forecasts of urban expansion to 2030 and direct impacts on biodiversity and carbon pools. Proceedings of the National Academy of Sciences 109:16083-16088. http://dx.doi.org/10.1073/pnas.1211658109
Shakeel, T., and T. M. Conway. 2014. Individual households and their trees: fine-scale characteristics shaping urban forests. Urban Forestry and Urban Greening 13:136-144. http://dx.doi.org/10.1016/j.ufug.2013.11.004
Shochat, E., P. S. Warren, S. H. Faeth, N. E. McIntyre, and D. Hope. 2006. From patterns to emerging processes in mechanistic urban ecology. Trends in Ecology and Evolution 21:186-191. http://dx.doi.org/10.1016/j.tree.2005.11.019
Sidique, S. F., F. Lupi, and S. V. Joshi. 2010. The effects of behavior and attitudes on drop-off recycling activities. Resources, Conservation and Recycling 54:163-170. http://dx.doi.org/10.1016/j.resconrec.2009.07.012
Sokal, R. R., and F. J. Rohlf. 1995. Biometry. Third edition. W.H. Freeman and Company, New York, New York, USA.
Steel, B. S., P. List, and B. Shindler. 1994. Conflicting values about federal forests: a comparison of national and Oregon publics. Society and Natural Resources 7:137-153. http://dx.doi.org/10.1080/08941929409380852
Steinberg, R. M., A. T. Morzillo, S. P. D. Riley, and S. G. Clark. 2015. People, predators, and place: rodenticide impacts in a wildland-urban interface. Rural Society 24:1-23. http://dx.doi.org/10.1080/10371656.2014.1001478
Sterrett, J., C. Ozawa, D. Ryan, E. Seltzer, and J. Whittington. 2015. Planning the Pacific Northwest. APA Press, Chicago, Illinois, USA.
Svoboda, E., E. Mika, and S. Berhie. 2008. America’s 50 greenest cities. Popular Science February 8, 2008. [online] URL: http://www.popsci.com/environment/article/2008-02/americas-50-greenest-cities?page=
Taylor, M. S., B. W. Wheeler, M. P. White, T. Economou, and N. J. Osborne. 2015. Research note: urban street tree density and antidepressant prescription rates - a cross-sectional study in London, UK. Landscape and Urban Planning 136:174-179. http://dx.doi.org/10.1016/j.landurbplan.2014.12.005
Tiebout, C. 1956. A pure theory of local expenditures. Journal of Political Economy 64:416-424. http://dx.doi.org/10.1086/257839
Tratalos, J., R. A. Fuller, P. H. Warren, R. G. Davies, and K. J. Gaston. 2007. Urban form, biodiversity potential and ecosystem services. Landscape and Urban Planning 83:308-317. http://dx.doi.org/10.1016/j.landurbplan.2007.05.003
Troy, A. R., J. M. Grove, J. P. M. O’Neil-Dunne, S. T. A. Pickett, and M. L. Cadenasso. 2007. Predicting opportunities for greening and patterns of vegetation on private urban lands. Environmental Management 40:394-412. http://dx.doi.org/10.1007/s00267-006-0112-2
United Nations, Department of Economic and Social Affairs, Population Division. 2014. World urbanization prospects: the 2014 revision, highlights (ST/ESA/SER.A/352). United Nations, New York, New York, USA. [online] URL: http://esa.un.org/unpd/wup/Highlights/WUP2014-Highlights.pdf
United States Department of Commerce (USDC). 2014. U.S. Census Bureau data. American Factfinder, commuting characteristics. United States Department of Commerce, Washington, D.C., USA. [online] URL: http://www.factfinder.census.gov
Van Liere, K. D., and R. E. Dunlap. 1980. The social bases of environmental concern: a review of hypotheses, explanations and empirical evidence. Public Opinion Quarterly 44:181-197. http://dx.doi.org/10.1086/268583
Vaske, J. J., M. P. Donnelly, D. R. Williams, and S. Jonker. 2001. Demographic influences on environmental value orientations and normative beliefs about national forest management. Society and Natural Resources 14:761-776. http://dx.doi.org/10.1080/089419201753210585
Yabiku, S. T., D. G. Casagrande, and E. Farley-Metzger. 2008. Preferences for landscape choice in a southwestern desert city. Environment and Behavior 40:382-400. http://dx.doi.org/10.1177/0013916507300359
Yeakley, J. A. 2014. Urban hydrology in the Pacific Northwest. Pages 59-74 in J. A. Yeakley, K. G. Mass-Hebner, and R. M. Hughes, editors. Wild salmonids in the urbanizing Pacific Northwest. Springer, New York, New York, USA. http://dx.doi.org/10.1007/978-1-4614-8818-7_5
Yeakley, J. A., R. M. Hughes, and K. G. Maas-Hebner, editors. 2014. Wild salmonids in the urbanizing Pacific Northwest. Springer, New York, New York, USA. http://dx.doi.org/10.1007/978-1-4614-8818-7
Zhu, W.-X., N. D. Dillard, and N. B. Grimm. 2004. Urban nitrogen biogeochemistry: status and processes in green retention basins. Biogeochemistry 71:177-196. http://dx.doi.org/10.1007/s10533-004-9683-2
Zick, C. D., K. R. Smith, J. X. Fan, B. B. Brown, I. Yamada, and L. Kowaleski-Jones. 2009. Running to the store? The relationship between neighborhood environments and the risk of obesity. Social Science and Medicine 69:1493-1500. http://dx.doi.org/10.1016/j.socscimed.2009.08.032