The Effects of Historical Housing Policies on The Effects of Historical Housing Policies on Resident Exposure to Intra-Urban Heat: A Study of Resident Exposure to Intra-Urban Heat: A Study of 108 US Urban Areas 108 US Urban Areas

: The increasing intensity, duration, and frequency of heat waves due to human-caused climate change puts historically underserved populations in a heightened state of precarity, as studies observe that vulnerable communities—especially those within urban areas in the United States—are disproportionately exposed to extreme heat. Lacking, however, are insights into fundamental questions about the role of historical housing policies in cauterizing current exposure to climate inequities like intra-urban heat. Here, we explore the relationship between “redlining”, or the historical practice of refusing home loans or insurance to whole neighborhoods based on a racially motivated perception of safety for investment, with present-day summertime intra-urban land surface temperature anomalies. Through a spatial analysis of 108 urban areas in the United States, we ask two questions: (1) how do historically redlined neighborhoods relate to current patterns of intra-urban heat? and (2) do these patterns vary by US Census Bureau region? Our results reveal that 94% of studied areas display consistent city-scale patterns of elevated land surface temperatures in formerly redlined areas relative to their non-redlined neighbors by as much as 7 ◦ C. Regionally, Southeast and Western cities display the greatest di ﬀ erences while Midwest cities display the least. Nationally, land surface temperatures in redlined areas are approximately 2.6 ◦ C warmer than in non-redlined areas. While these trends are partly attributable to the relative preponderance of impervious land cover to tree canopy in these areas, which we also examine, other factors may also be driving these di ﬀ erences. This study reveals that historical housing policies may, in fact, be directly responsible for disproportionate exposure to current heat events.


Introduction
No other category of hazardous weather event in the United States has caused more fatalities over the last few decades than extreme heat [1]. In fact, extreme heat is the leading cause of summertime morbidity and has specific impacts on those communities with pre-existing health conditions (e.g., chronic obstructive pulmonary disease, asthma, cardiovascular disease, etc.), limited access to resources, and the elderly [2][3][4]. Excess heat limits the human body's ability to regulate its internal temperature, which can result in increased cases of heat cramps, heat exhaustion, and heatstroke and may exacerbate other nervous system, respiratory, cardiovascular, genitourinary, and diabetes-related conditions [5]. As heat extremes in urban areas become more common, longer in duration, and more intense across the US and globe [6,7] due to unmitigated human emissions of investment such as the privileging of the suburban highway system at the expense of the city's public transportation [25].
Similarly, as areas that received severely limited real estate investment over time, we might expect those areas to have fewer environmental amenities that help to clean and cool the air, including urban tree canopy [26]. Recent studies describe the increased likelihood that those who are poor and communities of color are more likely living in areas with fewer trees and poorer air quality [27,28]. At the same time, the extent to which these policies may have resulted in environmental disparity as a consequence of systematic disinvestment nationally largely remains an open question. We seek here to assess if evidence of disproportionate environmental stressors (specifically anomalous urban land surface temperatures) exists through the lens of these long-term housing policies, and if a national-scale signal varies by region in the US.
By assessing HOLC maps from aggregated urban areas in the United States ( Figure 1) in relation to the relative anomaly of land surface temperature within and outside redlined areas, we ask two questions: (1) do historical policies of redlining help to explain current patterns of exposure to intra-urban heat in US cities? and (2) how do these patterns vary by geographic location of cities? Our intent is not to explain why precisely these patterns exist; instead, we seek to describe their relation through spatial analysis of historical redlining maps and present-day warm season intra-urban land surface temperature anomalies. By examining these patterns, we aim to assess how current patterns of intra-urban heat inequities may result from a combination of historical policies that may be further exacerbated by present-day planning practices that fail to center communities that have been historically underserved in adaptation and mitigation of these patterns. including urban tree canopy [26]. Recent studies describe the increased likelihood that those who are poor and communities of color are more likely living in areas with fewer trees and poorer air quality [27,28]. At the same time, the extent to which these policies may have resulted in environmental disparity as a consequence of systematic disinvestment nationally largely remains an open question.
We seek here to assess if evidence of disproportionate environmental stressors (specifically anomalous urban land surface temperatures) exists through the lens of these long-term housing policies, and if a national-scale signal varies by region in the US. By assessing HOLC maps from aggregated urban areas in the United States ( Figure 1) in relation to the relative anomaly of land surface temperature within and outside redlined areas, we ask two questions: (1) do historical policies of redlining help to explain current patterns of exposure to intraurban heat in US cities? and (2) how do these patterns vary by geographic location of cities? Our intent is not to explain why precisely these patterns exist; instead, we seek to describe their relation through spatial analysis of historical redlining maps and present-day warm season intra-urban land surface temperature anomalies. By examining these patterns, we aim to assess how current patterns of intra-urban heat inequities may result from a combination of historical policies that may be further exacerbated by present-day planning practices that fail to center communities that have been historically underserved in adaptation and mitigation of these patterns.

Materials and Methods
We use the University of Richmond's Digital Scholarship Lab's "Mapping Inequality" database ( Figure 2a, Richmond, VA, USA, [29]) to download each available city's HOLC map shapefile individually (n = 239). To make analysis of Landsat-derived LST maps less computationally complex, we then condense the 239 unique HOLC maps into a database of 108 US cities or urban areas that overlap within Landsat 8 imagery tiles, and excluding any cities that were not mapped with at least one of all four HOLC security rating categories (n = 4). In some cases, HOLC map shapefile boundaries needed to remove overlapping security rating boundaries, boundary crossings over bodies of water, and to merge overlapping maps drawn in the same generalizable urban area and/or because they were drawn during different years (Supplementary Materials I).

Materials and Methods
We use the University of Richmond's Digital Scholarship Lab's "Mapping Inequality" database ( Figure 2a, Richmond, VA, USA, [29]) to download each available city's HOLC map shapefile individually (n = 239). To make analysis of Landsat-derived LST maps less computationally complex, we then condense the 239 unique HOLC maps into a database of 108 US cities or urban areas that overlap within Landsat 8 imagery tiles, and excluding any cities that were not mapped with at least one of all four HOLC security rating categories (n = 4). In some cases, HOLC map shapefile boundaries needed to remove overlapping security rating boundaries, boundary crossings over bodies of water, and to merge overlapping maps drawn in the same generalizable urban area and/or because they were drawn during different years (Supplementary Materials I).
We assess patterns of intra-urban land surface temperatures in the 108 HOLC areas using readily-accessible Landsat 8 satellite-derived northern hemisphere summertime (June-August) land surface temperatures (LSTs) following accepted United States Geological Survey calculation protocol (30 × 30 m resolution, TIRS Band 10, Normal Difference Vegetation Index [NDVI] emissivity corrected LST, Figure 2b [20,30,31]. This LST method relies on transforming raw Landsat 8 TIRS Band 10 data into top-of-atmosphere spectral radiance and then into at-sensor brightness temperatures. LST is then calculated by correcting the at-sensor brightness temperatures by surface emissivity calculated from the NDVI (derived from Bands 4 and 5 [30]). LST maps were only generated from imagery that satisfied a threshold for less than 10 percent scene cloud coverage and had to have been collected in the northern hemisphere summertime between 2014 and 2017. While these LST descriptions of intra-urban heat are coarse in spatial resolution and not the most representative of human-level, experiential air temperatures which are better resolved by dense networks of air temperature and humidity monitors [13,32], LST maps such as these have been widely applied to questions of large-scale patterns related to urban land use and heat-related public health outcomes for individual US cities [20,33].
We then use Zonal Statistics in ESRI's ArcGIS Spatial Analyst toolbox to estimate the mean of the derived Landsat 8 LSTs within each individual HOLC security rating polygon within a given urban area (e.g., Figure 2b,c). We then estimate each individual HOLC security rating polygon's land surface temperature anomaly from the area-wide mean LST from all HOLC security rating polygons (referred to as δLST, Equation (1)).
This δLST estimate gives us the ability to show relatively how much warmer or cooler a particular HOLC security rating polygon is from the entire set of HOLC security rating polygons for a given urban area, and then compare these anomalies between cities in a quantitative manner.
We also estimate average percent developed impervious surface land cover [34] and tree canopy cover [35] within each HOLC polygon (Figure 2e,g) in each urban area as derived from the National Land Cover Database (NLCD) 2011 [36]. NLCD tree canopy percent is a 30 m raster dataset covering the coterminous United States, providing continuous percent tree canopy estimates derived from multi-spectral Landsat imagery for each 30 m pixel. NLCD imperviousness reports the percentage of urban developed surfaces that is impervious over every 30 m pixel in the coterminous United States and beyond. These estimates of underlying land use and overlying tree canopy may not sum to 100 percent, as tree canopy can exist over all land use types within a HOLC polygon and not all land use is necessarily impervious.
To compare δLST variations within and among HOLC security ratings between cities, we then average the estimated δLST by HOLC security rating category within each city. This binning by HOLC category yields how δLST varies between HOLC security ratings within each city. We then binned the δLSTs for each city at the national scale (n = 108) and by US Census Bureau regions: Northeast (n = 26), South (n = 29), Midwest (n = 41), and Western (n = 12). To estimate the significance of mean temperature differences between the HOLC security ratings by region and nationally, we apply a post-hoc ANOVA multiple comparisons test known as Tukey's Honest Significant Differences (HSD) Test. Tukey's HSD test estimates differences among group sample means for statistical significance. This pairwise post-hoc ANOVA test determines the statistical significance of differences between the mean of all pairs of group means using a studentized range distribution.  (1)), (d) box-whisker plot of the δLSTs presented in (c) binned by HOLC security rating (see Introduction text for explanations of designations), (e) percent tree canopy from NLCD 2011 [36] averaged into HOLC polygons, (f) box-whisker plot of the δLSTs presented in (e) binned by HOLC security rating, (g) percent developed impervious surface from NLCD 2011 [36] averaged into HOLC polygons, (h) box-whisker plot of the average imperviousness presented in (g) binned by HOLC security rating.

Results
Our LST maps were generated from Landsat 8 acquisitions that satisfied a < 10 percent scene cloud coverage threshold collected from 3 June 2014 to 25 August 2017 (Supplementary Materials  Table S1). These mostly sunny days provide the best conditions for Landsat 8 to reliably capture a strong LST pattern in urban areas [32]. Approximately 40 percent of the Landsat 8 imagery was collected during the 2016 northern hemisphere summer, while ~10 percent of the imagery was collected during the 2014 northern hemisphere summer. Regression tests reveal an insignificant  (1)), (d) box-whisker plot of the δLSTs presented in (c) binned by HOLC security rating (see Introduction text for explanations of designations), (e) percent tree canopy from NLCD 2011 [36] averaged into HOLC polygons, (f) box-whisker plot of the δLSTs presented in (e) binned by HOLC security rating, (g) percent developed impervious surface from NLCD 2011 [36] averaged into HOLC polygons, (h) box-whisker plot of the average imperviousness presented in (g) binned by HOLC security rating.

Results
Our LST maps were generated from Landsat 8 acquisitions that satisfied a < 10 percent scene cloud coverage threshold collected from 3 June 2014 to 25 August 2017 (Supplementary Materials Table  S1). These mostly sunny days provide the best conditions for Landsat 8 to reliably capture a strong LST pattern in urban areas [32]. Approximately 40 percent of the Landsat 8 imagery was collected during the 2016 northern hemisphere summer, while~10 percent of the imagery was collected during the 2014 northern hemisphere summer. Regression tests reveal an insignificant relationship between the day that the imagery was collected and the resulting δLST patterns (Supplementary Materials Table S1).
Our analysis reveals three major trends that help to address our research questions. First, LST differences across the cities follow a non-uniform distribution of differences, suggesting that historical redlining policies are reflected in present-day intra-urban heat differentially (Supplementary Materials  Table S1). Notable, intra-city δLST differences between areas given "D" and "A" HOLC security ratings range between +7.1 • C (Portland, OR) to −1.5 • C (Joliet, IL, USA), with~94% of urban areas included in this study showing warmer present-day LSTs in their "D"-rated areas relative to their "A"-rated areas (Supplementary Materials Table S1). While Portland (OR) and Denver (CO) had the greatest "D" to "A" security rating differences within a city, the warmest δLST temperatures in formerly redlined areas relative to the city-wide average LST were identified in Chattanooga (TN, 3.3 • C) and Baltimore (MD, 3.2 • C). These cities were in contrast to formerly redlined areas that displayed, on average, cooler surface temperatures than their non-redlined counterparts (e.g., Joliet, IL, USA and Lima, OH, USA), a consistent pattern in several cities across the Midwest (Supplementary Materials Table S1). Patterns of relatively pronounced or muted δLST are underscored by attendant patterns of land use type and cover within the same HOLC security rating polygons, whereby the urban areas with the highest D-A difference and largest δLST in D-rated polygons show considerable HOLC rating-specific trends in average tree canopy and developed impervious surface percentages as compared to the Midwestern cities that exhibit cooler-than-average δLST patterns in their D-rated areas (Supplementary Materials Figure S1). The coolest δLST temperatures in areas assigned "A" HOLC security ratings relative to the city-wide average LST were identified in Birmingham (AL, −4.7 • C) and Roanoke (VA, −4.5 • C).
Regional aggregation of the city-specific trends reveals that average δLST differences between HOLC security rating categories exhibit a pattern of incremental warming relative to worsening HOLC security rating (Figure 3b-e). However, the magnitude of the δLST differences varies considerably by region, with the Midwest (n = 41) showing more muted δLST differences than the Southeast (n = 29) and West (n = 12), respectively (Figure 3b-e). Honest Significant Difference tests on urban areas at the regional scale reveal that the greatest δLST differences exist between "A" and "D" HOLC security rating areas across US regions, with "D"-rated areas progressively warmer than each subsequent rating in the present day. These amplified differences in the West and Southeast, as well as the relatively muted response in the Midwest (Figure 3b-e), are attended by similar differences in underlying percent land use cover (Figure 4b-e), and especially apparent in the available tree canopy (Figure 5b-e) for the areas assigned "A" HOLC security ratings.
A third trend that is consistent in a national-scale aggregation of δLSTs in these cities is the finding that "D"-rated areas are now on average 2.6 • C warmer than "A"-rated areas (Figure 3a). Each HOLC security rating category warms systematically relative to the more favorable neighbor security rating category (Figure 3a). Honest Significant Difference tests reveal that areas given "D" HOLC security ratings are significantly warmer than all of the other HOLC security rating categories at the national scale, in progressively larger magnitudes. These LST differences are underscored by similar, but opposing, national-scale patterns in underlying land use and tree canopy within the same redlined cities (Figures 4a and 5a), showing that areas assigned a "hazardous" HOLC security rating in US cities exhibit quantitatively less coverage by tree canopy and more coverage by impervious surfaces in the present decade [35,36].

Discussion and Conclusions
We sought to understand the extent to which historic policies of redlining help to explain current patterns of intra-urban heat and the extent to which these patterns were consistent across US cities. Questions about the increasing economic inequality in US society motivated our inquiry and suggest several patterns related to historical federal housing policies and which communities experience the hottest areas of a city in the present day. Most notably, the consistency of greater temperature in formerly redlined areas across the vast majority (94%) of the cities included in this study indicates that current maps of intra-urban heat echo the legacy of past planning policies. While earlier studies document the lack of present-day services for and lower income of communities living in formerly redlined areas, this analysis presents an argument for understanding how global climate change will further exacerbate existing, historically-codified inequities in the US. We highlight three important dimensions of our findings-built environment, policies, and current inequities-as they relate to implications of these results.
First, our findings corroborate earlier studies that describe consistent patterns between the lack

Discussion and Conclusions
We sought to understand the extent to which historic policies of redlining help to explain current patterns of intra-urban heat and the extent to which these patterns were consistent across US cities. Questions about the increasing economic inequality in US society motivated our inquiry and suggest several patterns related to historical federal housing policies and which communities experience the hottest areas of a city in the present day. Most notably, the consistency of greater temperature in formerly redlined areas across the vast majority (94%) of the cities included in this study indicates that current maps of intra-urban heat echo the legacy of past planning policies. While earlier studies document the lack of present-day services for and lower income of communities living in formerly redlined areas, this analysis presents an argument for understanding how global climate change will further exacerbate existing, historically-codified inequities in the US. We highlight three important dimensions of our findings-built environment, policies, and current inequities-as they relate to implications of these results.
First, our findings corroborate earlier studies that describe consistent patterns between the lack of tree canopy and historically underserved urban areas, at the national and regional scales (Figures 4  and 5). The prevalence of impervious surfaces as opposed to tree canopy points to the fact that green spaces have been consistently more abundant in wealthier and majority White-identifying neighborhoods [26]. At the same time, intra-urban heat is not only affected by tree cover, since the use of different materials within varying urban typologies also amplifies temperatures [19,37]. Two features of the urban landscape-roadways and large building complexes-are well known to transform solar radiation into heat. These landscape features absorb the energy-filled short-wave radiation coming from the sun, and re-emit long-wave radiation during the diurnal heating-cooling process. As a result, large roadways and building complexes gain heat during the day and, as the evening cools ambient temperatures, the retained heat is released back into the neighborhoods, which is captured by overhead satellite sensors. These evening temperatures are precisely the factors that can exacerbate excess mortality and morbidity [38].
An earlier body of evidence from the regional studies and economics literature makes the connection between federal programs that provided incentives for major roadway and building construction projects and the fact that many of these occurred in the lowest income neighborhoods of cities [39][40][41]. In fact, the 1950s were an important decade for the creation of major roadways across the US, and many redlined neighborhoods were transformed and divided by road and highway infrastructure projects [42]. These changes came at a time when intra-urban heat was not recognized as a major public health hazard, and yet, given the well-known heat-absorbing capacity of asphalt and concrete [43], the selection of these materials may underlie the differences revealed in these results.
Similarly, throughout the mid-1900s large building complexes, including housing complexes, industries, and university campuses, often subsidized by the federal government, were also placed in redlined areas, largely due to the inexpensive land, and current population of largely lower income and communities of color [44]. From the 1940s through the 1970s, large buildings were made of high-density materials, such as cinder block and brick, which retain heat, and maintain high temperatures through the night [45,46]. Many of these buildings still stand, and the LST maps investigated here partially describe the thermal signature of these buildings. Areas that were in non-redlined areas, often built of other materials but also dispersed across a more natural, maintained landscape, which allows for greater circulation of air [47,48] are hence the cooler neighborhoods registered by satellites.
Second, differences in implementing policies and landscapes may help to explain the variation of temperatures across different regions of the US. The cities of Portland (OR), Denver (CO), and Minneapolis (MN), for example, notably reflect the largest differences between the formerly redlined areas and their non-redlined counterparts (Supplementary Materials Table S1). We can speculate that the redlined areas of all three cities are currently located in areas with extensive physical infrastructure, including housing complexes, railway terminals, industrial or manufacturing sites, and/or adjacent to major business centers. The presence of these current day land uses may suggest a relationship between formerly inexpensive land and large-scale development. These results, when combined with more pernicious modern-day policies that support development of high-asphalt and low tree canopy areas such as massive shopping complexes that contain large surface parking lots, are further strengthened. In Portland (OR), for example, decades of development code allowed for multifamily complexes to cover 100% of the lot area with no provisions for greening. Only recently, and due to extensive support from local researchers and community organizations did the city evaluate earlier asphalt-driving policy to require 85% lot coverage and green spaces [49,50]. Such reversals of policy are the forms of planning that can help to reverse decades of amplifying temperatures in areas that have historically been underserved. Denver and Minneapolis are also making strides, though without further understanding about the historic and present-day drivers that generate these asphalt-rich and tree canopy-poor land uses on intra-urban heat, and local communities, progress will be slow.
In addition, the coupling of landscape and historic designs of urban development in these cities may also play a role in helping to explain differences across the country. Portland, like Minneapolis, are in landscapes where tree canopy is relatively easy to sustain. Unlike arid and drought-prone areas, where planting trees can require extensive maintenance, the warm, sunny summers and wet/snowy winters of Portland, Minneapolis and other cities of the Northwest and Midwest, provide ideal conditions for expanding an urban forest, which can, in turn, reduce surface temperatures of a neighborhood. Tree planting efforts often took place as part of urban development projects in the early and mid-1900s, and were used as a way to mark special designations [42]. Similarly, metropolitan areas that conform to the concentric zone model (for example, places like Chicago, Los Angeles, and Philadelphia) tend to be larger and more densely populated metros, often with a higher degree of both affluence and inequality, a larger African American population, and a greater share of population in the suburbs. In the remaining metropolitan areas, there is greater integration between the affluent and the poor [44]. In these places, such as Seattle (WA), Charleston (WV), and Birmingham (AL), the rich are concentrated in the urban core, where redlining and tree planting efforts coincide.
Finally, indicators of and/or higher intra-urban LSTs have been shown to correlate with higher summertime energy use [51,52], and excess mortality and morbidity [20,53,54]. The fact that residents living in formerly redlined areas may face higher financial burdens due to higher energy and more frequent health bills further exacerbates the long-term and historical inequities of present and future climate change. As the results from earlier studies have documented income inequality between formerly redlined areas another other parts of US cities, we recognize that hotter areas will amplify these current inequities. Such historic income inequality leads to income segregation because higher incomes, which are further supported by past and current housing policy, allow certain households to sort themselves according to their preferences-and control local political processes that continue exclusion [55]. Other explanatory factors of these patterns, though too many for the current study and setting the stage for future studies, include disinvestment in urban areas, suburban investment and land use patterns, and the practices generally of government and the underwriting industry [39,56].
To our knowledge, this is the first study to link a historical federal housing policy to the creation (or at least the exacerbation) of a climate stressor and potential variability in resident exposure to it. While redlining most likely did not create the microenvironments that mediate LSTs relative to the rest of the urban environment, our findings suggest a strong and significant likelihood of the cauterization of current day exposure to the hottest parts of a city. While patterns of who experiences the most exposure to intra-urban heat may change as a result of (green) gentrification, which many formerly redlined neighborhoods are undergoing (e.g., wealthier communities can afford to green and change the physical landscape, and, over time, cool the hottest areas of a city), we observe consistent patterns that can be inferred as in part due to the creation of HOLC maps [23]. Future studies will need to describe the mechanisms by with planning practices-past and present-are likely to amplify the effects of climate change on historically underserved communities and communities of color.
While a growing body of evidence describes the intra-urban variation of temperatures due to characteristics of the built environment, few have asked why we observe a pattern of historically-marginalized communities living in the hottest areas. Here we have presented results from an analysis of 108 US cities that aimed to examine the role of historic "redlining" policies in mediating exposure to intra-urban heat. We found that in nearly all cases, those neighborhoods located in formerly redlined areas-that remain predominantly lower income and communities of color-are at present hotter than their non-redlined counterparts. Although the extent of differences in temperatures varies by region, the preponderance of evidence establishes that those experiencing the greatest exposure to present and potentially future extreme heat are living in neighborhoods with the least social and ecosystem services historically.
As more and more communities race to develop plans to react to and adapt to worsening extreme heat and its attendant effects on human health [57], a research agenda focused on developing place-specific, heat-mitigating urban designs and interventions [58][59][60][61] will be critical toward not only alleviating heat disparity but ensuring that the urban forms and policies that gave rise to these inequities in our past (like redlining) are recognized and altogether avoided. Furthermore, crafting climate equity-centered policies that recognize decades of disproportionate exposure to environmental stressors can help any new discoveries in urban design get implemented with focus and rapidity.
Supplementary Materials: The following are available online at http://www.mdpi.com/2225-1154/8/1/12/s1, Figure S1: Comparison of urban areas of relatively large or small differences in LSTs between HOLC grades, Table S1: Urban area-specific results from our LST analysis.
Author Contributions: J.S.H. conceived the project and coordinated the analysis, advised interpretation, and contributed to the manuscript, created figures, and coordinated the responses to reviewers. V.S. provided major contributions to the manuscript including context, interpretation, editorialization, and literature review and references. N.P. performed HOLC map and satellite imagery download and spatial analyses. All authors have read and agreed to the published version of the manuscript.
Funding: This research involved no external funding.