Green space is vital for supporting biodiversity across urban and suburban landscapes [1
]. Formal green spaces set aside for nature, such as parks, gardens, and forest preserves, can benefit both wildlife and people; however, informal green spaces, such as brownfields, vacant lots, street verges, and powerline corridor rights-of-way, can also be equally if not more important sources of habitats [2
]. While informal greenspaces in developed landscapes can support substantial biodiversity, they are understudied systems [4
Electric transmission powerline corridors are a category of informal greenspace that has the potential to contribute greatly to biodiversity in cities because they are generally managed by a single or a few stakeholders, are linear tracts that could increase connectivity between other green spaces, and can encompass large areas. In 2015, there were approximately 642,000 circuit miles of high-voltage transmission lines in the United States [6
], which translates to hundreds of thousands of linear kilometers of electric right-of-way corridors, encompassing between 2 and 3 million hectares of land across the country [7
]. Electric transmission corridors have unique requirements for management because vegetation must be kept from touching the powerlines [8
]. Because of this, powerline corridors are generally maintained as perpetual early-successional or frequently disturbed habitats. Vegetation management in powerline corridors can take many forms, including grass- or brush-mowing, pruning, spot-spraying or blanket-spraying of herbicides [9
], or even burning [10
]. Many electric companies state a commitment to protecting or sustaining ecosystems, and a national public–private agreement was recently developed to promote voluntary conservation efforts on energy and transportation lands [11
]. Therefore, it is important that vegetation management within powerline corridors supports these policies. If vegetation management is done effectively, powerline corridors may provide a huge amount of land area for species that require early-successional habitats, including many pollinators [12
] and grassland and shrubland birds [13
Several studies have examined the effects of powerline corridor vegetation management on biodiversity, e.g., [7
], but there is not a consistent answer as to which management strategy is best for biodiversity overall, as it may be taxon- and context-specific. In some cases, the frequent disturbances inherent in powerline corridor management can support an increase in invasive plant cover (e.g., [16
]); in other situations, native vegetation, such as tallgrass prairie plants, can thrive (e.g., [17
]). Depending on the management of a powerline corridor and its effects on vegetation species richness, there is evidence for an increase in [7
], mixed response of [19
], or no effect on [20
] the species richness of bees and butterflies in and around the corridor as compared to surrounding natural habitats.
Like powerline corridors, residential yards and gardens are widely distributed and account for a large proportion of green space, particularly in urban and suburban environments [21
]. In some urban areas, residential yards are the single largest contributors to green space (e.g., [22
]). Although individual yards are relatively small, when viewed together, they can be envisioned as the backbone of the green urban and suburban matrix. As with powerline corridors, the vegetation in residential yards is generally characterized by routine management (although residential yard management varies widely, and they may be mown more frequently than corridors). This makes yards more similar to powerline corridors than the undisturbed “natural” habitats to which they are more often compared in the literature (e.g., [18
]). Therefore, due to their wide distribution and frequent management, habitats in residential yards provide an ideal baseline of comparison for green space in developed landscapes. If powerline corridors can support different or greater levels of biodiversity than those found in yards, they add ecological value to the urban or suburban landscape. Very few previous studies have actually examined the ecology of powerline corridors in the context of residential landscapes despite the increasing importance of residential areas in the face of expanding global urbanization and suburbanization [28
The goal of our study was to compare biodiversity in suburban powerline corridors to the biodiversity found in the surrounding residential yard matrix, focusing on three taxa: plants, birds, and bees/wasps/lepidopterans (hereafter, “insect pollinators”). We also compared corridors managed in three different ways: (1) mowed frequently and maintained as lawn, (2) brush mowed approximately every five years, with vegetation allowed to establish and grow spontaneously between mowing events, and (3) restored and/or maintained as native prairie habitat. We compared the biodiversity in these corridors to the biodiversity in the surrounding residential neighborhoods. We hypothesized that vegetation management will significantly affect the added value of the corridor as a habitat for wildlife. We predicted that prairie sites will have different communities and higher overall biodiversity than the other sites, and yard sites would fall somewhere in between mown and prairie sites in terms of habitat quality. In addition, we predicted that differences in management would affect vegetation and floral resources, which would, in turn, affect bird and insect pollinator communities.
2. Materials and Methods
2.1. Study Region and Field Sites
Our study took place in the suburbs of Chicago, Illinois, USA, which is the third-largest metropolitan area in the United States. All of our study sites were located in DuPage and Will counties, two of the five “collar counties” surrounding the city of Chicago. These counties are mainly suburbanized/developed, although some areas to the south are used for agriculture [29
]. This region is characterized by a hot-summer humid continental climate and experiences four distinct seasons [30
]. Prairies are one of the major historical native habitat types in this region, although their prevalence and connectivity has been greatly decreased due to conversion to agriculture and urbanization [31
Our study areas were located in electric transmission right-of-way corridors owned by the Commonwealth Edison (ComEd) company, one of the largest landholders in the state of Illinois, USA. ComEd maintains over 22,945 hectares (56,698 acres) of electric transmission rights-of-way in Illinois, and the company has the authority to control how the vegetation in that land is managed (Amy Flansburg, personal communication, 7 December 2021).
These powerline corridors (hereafter, “corridors”) had a mean width of 65.5 m (range = 40–138 m). Vegetation in the corridors was managed in three different ways: (1) maintained as a prairie, (2) managed on a 5-year brush-mowing and herbicide cycle to remove trees and large shrubs, or (3) mowed low and managed as lawn/turf grass. Prairie sites were either restored de novo prior to our study or were located on remnant dolomite prairies. Prairie management during our study season was limited to spot-spray herbicide application to control invasive species. In previous years, the de novo restoration prairies were also managed through seeding, mowing, haying, herbicide application, and burning. Sites maintained on the 5-year cycle resembled old-field habitats (and, in fact, most were previously farmed); lawn-type sites were mowed with differing frequencies, but generally had no tall weeds or shrubs and had grassy vegetation under approximately 40 cm. All of the non-prairie (i.e., mown and old-field) corridor sites were located within suburban residential neighborhoods, while the prairie sites were located within or adjacent to county forest preserves (by necessity due to the fact that this is where all of the prairie corridors in the region are found).
We haphazardly selected three prairie, three old-field, and four mown corridors (to account for the short lengths of two of them) for a total of ten study corridors (Figure 1
A,B). All corridors were separated from each other by at least 0.5 km, although the majority were much farther from each other (Figure 1
A). At each study corridor, we selected either two or three study sites depending on the length of the corridor section; in all, we had a total of 28 sites spread across the ten corridors. Study sites within a corridor were separated from each other by approximately 300 m (Figure 1
C) to ensure spatial independence for both birds [32
] and insect pollinators [18
]. Owing to logistical constraints, we were unable to sample plants, insect pollinators, and birds at all of the study sites, although each taxon was surveyed in all three types of corridors. Birds were sampled at a subset of 23 sites and insect pollinators and plants were sampled at a subset of 19 sites.
In addition to corridor sites, we selected nearby residential yards for comparison to the non-prairie corridors. Residential comparison sites were different for birds than for insect pollinators and plants due to the need for sampling on different scales for each taxon, but all were between approximately 100 and 300 m from either a mown or old-field corridor where we surveyed birds or insect pollinators and plants. We haphazardly selected one bird comparison site on a street in a residential neighborhood near each mown and old-field corridor (n = 6 residential bird comparison sites). This allowed us to survey birds in multiple yards at once. In contrast, we chose five backyards in each of three neighborhoods near non-prairie corridors for insect pollinator residential comparison sites (15 total backyards). The backyards were chosen haphazardly based on homeowner permission. Because the backyards were smaller than the corridor sites, we treated the data for each cluster of residential backyards as a single site in order to compare sites with equal areas and sampling effort (n = 3 backyard “sites” from 15 backyards).
2.2. Insect Pollinator Surveys
To capture as much of the diversity in the insect pollinator communities as possible, we used two complementary survey methods: Pollard walks and pan traps [27
]. We set an 8 m transect for insect pollinator surveys in the center of the lawn in each backyard, and 40 m transects were established at each corridor site; therefore, each cluster of five residential backyard transects was of comparable length to one corridor site transect. Transects were used to conduct Pollard walks and to deploy pan traps.
During the Pollard walks, transects were walked at a consistent pace, and all Hymenoptera (excluding ants) and Lepidoptera within 5 m of the transect were identified and counted. In the corridors, each 40 m transect was walked for 30 min. In each residential backyard, 8 m transects were walked for 6 min. All Pollard walks were conducted by the same researcher, once in early summer (15 June through 6 July) and once in mid/late summer (4 August through 21 August). Walks were conducted between the hours of 8 a.m. and 3 p.m. on days that were partly or mostly sunny, with temperatures above 60 °F and wind speeds below 15 mph.
Pan traps, also known as bee bowls, were used to passively sample the insect pollinator community. We used small plastic bowls that were painted white, blue, yellow, or red and filled with a dilute solution of dish soap. Bowls were spaced evenly along the transect in each site, with 4 bowls (one of each color) placed along the transect in each backyard and 20 bowls placed along the transect in each corridor site. Bowls were deployed on the same day that Pollard walks were conducted and then collected on the following day, allowing roughly 24 h of passive sampling. The contents of the bowls were strained and placed in sealed containers with 70% ethanol solution. In the lab, we sorted, pinned, and identified the Hymenoptera (excluding ants) and Lepidoptera [34
]. While other insect orders, such as flies (Diptera) and beetles (Coleoptera), may also provide pollination services, we opted to include only Hymenoptera and Lepidoptera because our two sampling methods were designed to optimize collection of these orders only.
We pooled the data from both Pollard walks and pan traps for each site. Because we were unable to confidently identify all hymenopteran pollinators to the species level, we lumped our pollinator data collected from both Pollard walks and pan traps at the genus level for the insect pollinator genus richness per site. We were able to identify all lepidopterans to the species level, so we created a second response variable from a subset of the insect pollinator data describing the species-level richness of lepidopterans only at each site.
2.3. Plant Surveys
In July, we used the same transects established for the Pollard walks to conduct vegetation floristics surveys of each site. Ten 0.25 m2
quadrats were evenly spaced along the transects in the corridors, and two quadrats were evenly spaced along transects in the lawn in the backyards. We identified all plants within each quadrat to the lowest taxonomic level possible while in the field. Plants were later classified as native or non-native according to the USDA PLANTS database [38
]. We then determined both the total plant species richness and the native richness per site.
2.4. Bird Surveys
To survey birds, we conducted 10 min point counts at the center of each corridor site and at the residential comparison sites. During the point count, the observer recorded all birds seen or heard within a 100 m radius. At corridor sites, we recorded whether the birds were detected within or outside of the corridor.
Point counts were conducted after sunrise and no later than 9:30 AM at three times during the breeding season: early June (8–16 June), mid/late June (18–25 June), and late June/July (28 June–14 July). A minimum of eight days passed between each point count at a site. Each point count was conducted by a single experienced observer and took place only under appropriate weather conditions (i.e., no rain or strong wind).
We used these data to calculate the cumulative species richness per site (across all point counts) of all birds detected and the cumulative species richness per site of birds detected within the boundaries of the corridor. We normalized the corridor bird species richness by dividing the number of species detected within the corridor by the area of corridor within the 100 m radius buffer. This converted the corridor bird response variable into the number of bird species per hectare of corridor.
2.5. Environmental Covariate Data Collection
We collected data on environmental variables that we hypothesized would affect biodiversity within the sites: floral resources, vegetation density, and surrounding landcover. We measured floral resources twice per season at each pollinator site on the same days and transects as the Pollard walks. A single researcher estimated the percentage of surface area covered by blooming forbs within 5 m of each transect. We then characterized floral resources at each site by selecting the higher floral resource cover of the two visits as an estimate of peak bloom.
We measured vegetation density in corridors along a 50 m transect centered on each point count location and extending lengthwise along the corridor using a modified Robel pole [39
]. Robel pole measurements were taken at plots located every 5 m along each transect for a total of 10 plots per site. Robel pole measurements provide an estimate of standing biomass and vegetation structure [40
], which is often a significant predictor of bird habitat use [41
]. Our pole consisted of a 1.4 m length of a PVC pipe that was 2.13 cm in diameter with markings every 2.5 cm. An observer looked at the pole at a distance of 4 m and a height of 1 m and recorded the lowest marking on the pole that was not obscured by vegetation (even if that marking was visible only due to a gap in the vegetation and was obscured above that point). At each plot, we took Robel pole measurements in the four cardinal directions and measured the maximum live plant height within 20 cm of the pole. We then calculated the mean Robel pole measurement (hereafter, “vegetation density index”) for each site.
Finally, we digitized all impervious surfaces, trees/shrubs, and the area of the corridor within a 100 m radius of each point count location based on reference imagery from the National Agriculture Imagery Program (USDA NAIP) from 2019 (the most recent imagery available) [42
]. We then calculated the area of each of the two landcover categories, as well as the area covered by the corridor itself, within each 100 m radius buffer.
We used Shapiro–Wilk tests [43
] followed by ANOVA tests to determine whether the four site types (residential comparison site or mown, old-field, or prairie corridor) varied significantly across four environmental variables: (1) maximum floral resource cover; (2) vegetation density index; (3) area of tree or shrub cover within a 100 m radius of each site; (4) area of impervious surface cover within a 100 m radius of each site. When the ANOVA tests were significant, we used Tukey’s honest significance tests to examine pairwise differences among management categories for each environmental variable.
We analyzed the biodiversity at each site by quantifying the plant communities (all plants and native plants only), the bird communities (all birds detected within 100 m of each site and birds detected only within the corridor), and the insect pollinator communities (non-ant hymenopterans and lepidopterans, as well as lepidopterans alone), for a total of six response variables. Each response variable described the species (or genus) richness at each site. We chose richness rather than another index of biodiversity because it is both simple and easy to interpret [44
We conducted three types of analyses of the biodiversity at each site: (1) testing for an effect of site type on each of the six biodiversity response variables; (2) testing for the effects of environmental covariates on the biodiversity response variables; (3) examining the differences in community composition for each of the three study taxa. All analyses were conducted in R version 3.6.1 [45
We began by using Shapiro–Wilk tests [43
] to determine if each of the six response variables was normally distributed. We then used either ANOVA or Kruskal–Wallis non-parametric tests to determine whether site type significantly affected the richness of each response variable. We followed these up with Tukey’s honest significant difference or pairwise Wilcoxon rank sum tests to determine whether there were significant differences between each site type. The p
-value adjustment for the pairwise Wilcoxon rank sum tests followed Benjamini and Hochberg [46
Next, we used AICc ranking of models in a priori model sets to determine the most important predictors of insect pollinator genus richness, lepidopteran species richness, total bird species richness, and richness of birds/ha in the corridor. We did not create models of plant species richness because we hypothesized that site type would be the most important predictor of plant communities, which we tested in the previous analysis. We created each model set to include variables that we had hypothesized would affect each biodiversity response variable. Specifically, we hypothesized that vegetation density and landscape context would predict bird biodiversity, and floral resource availability would predict insect pollinator diversity; all model sets also included models with the management category as a predictor variable, as well as a null model. We centered and scaled (i.e., subtracted the mean and divided by the standard deviation) the landscape context variables in these models because they were on very different scales from those of the other predictor variables. We used linear mixed-effects models with site location as a random effect (see Supplementary Table S1
for the complete model sets tested for each response variable). We used AICc to select the most parsimonious model for each response variable. We present the coefficients for the top model when only no other models were within ΔAICc < 2 from the best-supported model; when more than one model was within 2 ΔAICc from the top model, we present the model-averaged coefficients from the entire model set.
Finally, we characterized the communities for each taxon at each site based on the presence/absence of species. We examined insect pollinator genera, bird species within the corridor, and all plant species. We used the Jaccard index to calculate the dissimilarity among communities. We visualized community similarity using non-metric multi-dimensional scaling (NMDS) plots and calculated species vectors with 999 permutations. All multivariate analyses were performed using the R package “vegan” [47
During our surveys, we detected 114 plant species, 60 genera of insect pollinators, and 50 species of birds. We recorded 586 individual insect pollinators during the Pollard walks across all sites and collected 2127 individual insect pollinators in the pan traps. We counted 2202 individual birds during the point counts. The full species/genus lists are available in Supplementary Tables S2–S4
The site types varied significantly (p
< 0.05) across all four environmental variables (Figure 2
A–D). The old-field corridor sites had the highest floral resource cover, and both prairie and old-field corridor sites had a significantly higher vegetation density index than the mown corridor sites. Residential bird comparison sites tended to have more tree/shrub cover and more impervious surface cover nearby than corridor sites, and residential insect pollinator comparison sites had low levels of floral resource cover.
All biodiversity response variables varied significantly contingent on site type (Figure 3
). For plants, there was a striking difference between prairie and old-field sites versus the residential and mown corridors, with the former having significantly higher species richness (Figure 3
C,D). For birds and insect pollinators, the differences were a little less pronounced, but the richnesses were higher in the prairie and/or old-field corridors than in the mown or residential sites (Figure 3
Floral cover was the best predictor variable of both insect pollinator genus richness and lepidopteran species richness (Table 1
). In both cases, richness significantly increased with maximum floral cover. Although the site type was included in a model of lepidopteran species richness that was within ΔAICc < 2 of the top model, the 95% confidence intervals for that variable overlapped with zero, and it was, therefore, not a significant predictor. The most parsimonious model of total bird species richness included site type, plant density index, and area of tree/shrub cover as predictor variables. In contrast, the most parsimonious model of corridor bird species richness included only the plant density index as a predictor variable (Table 1
). For both bird species richness variables, richness significantly increased with the plant density index.
The NMDS plots showed that ecological communities tended to cluster by site type (Figure 4
). Insect pollinator communities in prairie and old-field corridor sites were more similar to each other than to those in mown sites, while those in residential comparison sites showed similarities to those in both mown and old-field sites. Mown site communities were dominated by a wasp genus Vespula
(ground-dwelling yellowjackets), while prairie sites were associated with Monarch butterflies (Danaus plexippus
, the only species we detected in the genus Danaus
), a genus of skippers (Euphyes
), and bumblebees and yellow-faced bees (Bombus
, Figure 4
A). Plant communities in mown sites were similar to those in residential yards, but were clustered separately from those of prairie and old-field sites; old-field site communities were dominated by several non-native plant species, while significant species vectors in the prairie sites were mainly native species (Figure 4
B). Finally, within-corridor bird communities in mown sites tended to be dominated by American Robins (Turdus migratorius
), and old-field sites were dominated by Mourning Doves (Zenaida macroura
) and Common Grackles (Quiscalus quiscula
). In contrast, prairie communities were characterized by species such as Song Sparrows (Melospiza melodia
), Common Yellowthroats (Geothlypis trichas
), and Eastern Kingbirds (Tyrannus tyrannus
; Figure 4
C), although these species were found in old-field sites as well.
Our study demonstrates that, given proper vegetation management, powerline corridors can add ecological value to suburban landscapes in the Midwest region of the United States by supporting different and, often, more diverse communities with respect to the surrounding residential matrix. To our knowledge, this is the first modern study to explicitly compare biodiversity within a corridor to that found in the most commonly occurring suburban greenspace, residential yards (however, see [47
]). Our results further demonstrate that how vegetation is managed within suburban powerline corridors strongly impacts the biodiversity of insect pollinators, plants, and birds. We found that species or genus richness of birds, insect pollinators, and plants tended to be higher in prairie and/or old-field corridor sites than in mown corridor and/or residential comparison sites (Figure 3
). Prairie and old-field corridors, therefore, may be important sources of habitats for multiple taxa within developed landscapes. While prairies are native ecosystems in our study region, prairie-managed corridors are certainly not universally applicable. Therefore, we suggest that future studies should explore powerline corridors that are managed similarly to the dominant native low-structure ecosystems in other regions of the world to determine if our conclusions generally hold.
Several previous studies have similarly demonstrated that powerline corridors, often kept as an early successional habitat type, can support different types of communities from the surrounding landscape for groups such as bees (e.g., [48
]) and birds (e.g., [26
]). These studies differ from ours, however, in that they compared powerline corridors to surrounding natural habitats, such as forest or grassland. In contrast, we compared powerline corridors to surrounding residential suburban yards maintained with lawns and gardens. As in other studies, we found that that non-mowed corridors are a novel (or uncommon) habitat type within these landscapes. It thus makes sense that we found different communities in prairie and old-field corridors from those in residential comparison sites (Figure 4
). Mown corridors, on the other hand, had roughly the same species richness as the lawn in residential comparison sites for all three taxa, and indeed, the plant communities and floral resource availability were similar. This suggests that, at least from an ecological standpoint, mown corridors alone do not add significant ecological value to suburban landscapes. However, we note that had we sampled the vegetation in ornamental gardens in the backyards, we may have found an increased level of plant species richness, although likely not in native plant species richness because few native species were planted as ornamentals in our residential study sites.
Surprisingly, we found no significant difference in either total or native plant richness between prairie and old-field sites, although there was a trend toward higher plant richness in prairies (Figure 3
C,D). While the prairie corridor sites were managed to increase native plant species, they were not necessarily high-quality prairies, and the number of native plant species we detected per quadrat was much lower than that found in quadrats of the same size in another study of high-quality Illinois prairies [50
]. However, our prairie sites supported more plant species of conservation interest than the old-field sites, which were dominated by non-native and often invasive plant species (Figure 4
B). This pattern held for insect pollinator communities as well; for example, insect pollinator communities in old-field sites were characterized by non-native Apis
bees (European honeybee), while prairie communities were dominated by native lepidopterans, including the Monarch butterfly. Despite the prevalence of some non-native species, the old-field sites did show an increase in biodiversity over that found in mown corridors and residential sites. This may reflect the “unkempt” nature of these old-field corridors [51
] and suggests that both prairies and old-field sites provide novel habitats to the residential landscape.
Another unexpected finding was that old-field sites had significantly higher floral resources than prairie sites (Figure 2
A). Our old-field study sites tended to be dominated by weedy flowering plants that can produce many inflorescences late in the season, such as Prickly Lettuce (L. serriola
, Figure 4
]. While we attempted to capture peak bloom at all of our sites by measuring floral resources in both early and mid/late summer, it is possible that many prairie corridor plants were very early season bloomers; this would mean that due to our study design, we were unable to capture the full floral resource availability at sites throughout the entire season. Alternatively, if prairies begin blooming very early in the spring and continue throughout the entire summer, they may have more temporally consistent floral resources throughout the season, despite having fewer floral resources at any given time. We recommend that future research should measure floral resource availability more frequently throughout the growing season to ensure the capture of potentially transient flowering phenologies.
We found that the species richness of lepidopterans was significantly higher in prairie sites than in mown and residential sites, but the genus richness of bees, wasps, and lepidopterans together differed significantly only between old-field and mown sites. Our linear mixed-effects models indicated that insect pollinator and lepidopteran richness were driven by floral availability, as we had hypothesized based on the well-documented relationship between insect pollinators and floral resources [53
]. We had not hypothesized, however, that floral resources would be higher in old-field than in prairie corridors. The differences in patterns that we detected between the entire insect pollinator community and the lepidopteran subset may result from lepidopterans needing host plants to support their larval caterpillar life stage in addition to floral resources for adults [54
]. For instance, we detected seven species of lepidopterans in prairies that were absent from old-field sites, and several of those require native grasses or forbs as larval hosts. Other pollinators, such as bees, may not have these same requirements. Prairie sites, which are characterized by more native plant species, may, therefore, be better for lepidopterans in particular if they are able to provide both floral resources and larval host plants. Old-field sites, on the other hand, may provide more bare ground and be better suited for providing nesting habitats for ground-nesting bees [56
We found that the bird species richness within the corridors was significantly lower in mown than in old-field and prairie sites (Figure 3
). The insectivorous birds in our study are generalist consumers and, thus, are not dependent on any particular insects or their plant hosts, so the native plant species in prairie corridors may not provide particular benefits. Instead, as hypothesized due to the strong links between birds and vegetation structure [41
], bird richness was strongly correlated with the vegetation density index within each site (Table 1
). The vegetation density at old-field sites tended to be higher than in prairie sites, although not significantly so. This could be related to the time since brush-mowing at our old-field sites; because young trees and shrubs are removed on a five-year cycle, vegetation density should differ within old-field sites based on their position within the management cycle. In contrast, vegetation density in prairie sites may be more consistent across years (although this would depend on prairie management practices). Unfortunately, we did not have enough old-field sites at different stages within the management cycle to test this. Because of the strong relationship between bird richness and vegetation density, we might expect that bird richness across years may fluctuate more in old-field corridors while remaining more consistent in prairie corridors. We recommend that future research should consider the effect of temporal variation in this system in response to cyclical management practices.
One important limitation of our study was that we were unable to examine the effect of the larger landscape context on the biodiversity within our sites. Several studies have shown that landscape context may be an important factor in determining communities of plants, birds, and pollinators (e.g., [13
]). Unfortunately, in our study system, most prairie-managed corridors were located within forest preserves or, otherwise, surrounded by natural habitats. Similarly, most mown and old-field corridors were found in developed areas. This is due to the fact that stakeholders with property near a powerline corridor often have some say in how the corridor is managed. Because of these land-use patterns, we are unable to say how biodiversity levels might differ if the prairie sites were embedded in a residential matrix like the other corridor types. It is possible that prairie sites had high species richness only because they were surrounded by natural habitats. However, the fact that the variables describing surrounding tree cover and impervious surface cover were important only in the model of total bird (but not corridor bird) richness suggests that landscape context (at least at the scale we examined) is not the most important predictor of bird species richness in this system. Nonetheless, we hypothesize that even if prairie sites within a residential matrix are less diverse than those embedded in natural areas, they would still be more diverse than mown sites due to the increased vegetation density and floral resource availability found in prairie sites. We also recommend that future studies be conducted in areas where prairie-managed corridors are located outside of forest preserves in order to fully elucidate the effects of landscape context on corridor biodiversity.
Our study shows that, given appropriate vegetation management, powerline corridors can enhance biodiversity in suburban landscapes by providing novel habitat types that support many species that are not found in surrounding residential areas. Because powerline corridors encompass such a large land area both across the United States and globally, this represents a major opportunity for increasing biodiversity in developed landscapes. We recommend that, whenever possible, suburban powerline corridors should not be maintained as lawns. Both old-field and prairie corridors can support much higher levels of biodiversity, though prairie sites supported a greater variety of native species of conservation interest. We thus suggest that managers in the Midwest region of the United States looking specifically to support native and/or grassland specialist species should manage sites in transmission line corridors as prairies whenever possible.