ArticlePDF Available

Abstract and Figures

Understanding bat use of human-altered habitat is critical for developing effective conservation plans for this ecologically important taxon. Green roofs, building rooftops covered in growing medium and vegetation, are increasingly important conservation tools that make use of underutilized space to provide breeding and foraging grounds for urban wildlife. Green roofs are especially important in highly urbanized areas such as New York City (NYC), which has more rooftops (34%) than green space (13%). To date, no studies have examined the extent to which North American bats utilize urban green roofs. To investigate the role of green roofs in supporting urban bats, we monitored bat activity using ultrasonic recorders on four green and four conventional roofs located in highly developed areas of NYC, which were paired to control for location, height, and local variability in surrounding habitat and species diversity. We then identified bat vocalizations on these recordings to the species level. We documented the presence of five of nine possible bat species over both roof types: Lasiurus borealis, L. cinereus, L. noctivagans, P. subflavus,andE. fuscus. Of the bat calls that could be identified to the species level, 66% were from L. borealis. Overall levels of bat activity were higher over green roofs than over conventional roofs. This study provides evidence that, in addition to well documented ecosystem benefits, urban green roofs contribute to urban habitat availability for several North American bat species.
Content may be subject to copyright.
Global Ecology and Conservation 4 (2015) 349–357
Contents lists available at ScienceDirect
Global Ecology and Conservation
journal homepage:
Original research article
Green roofs provide habitat for urban bats
K.L. Parkins , J.A. Clark
Department of Biological Sciences, Fordham University, 441 East Fordham Road, Bronx, NY, 10458, USA
article info
Article history:
Received 2 June 2015
Received in revised form 22 July 2015
Accepted 23 July 2015
Acoustic monitoring
Green roof
Urban ecology
Urban wildlife
Understanding bat use of human-altered habitat is critical for developing effective conser-
vation plans for this ecologically important taxon. Green roofs, building rooftops covered in
growing medium and vegetation, are increasingly important conservation tools that make
use of underutilized space to provide breeding and foraging grounds for urban wildlife.
Green roofs are especially important in highly urbanized areas such as New York City (NYC),
which has more rooftops (34%) than green space (13%). To date, no studies have exam-
ined the extent to which North American bats utilize urban green roofs. To investigate the
role of green roofs in supporting urban bats, we monitored bat activity using ultrasonic
recorders on four green and four conventional roofs located in highly developed areas of
NYC, which were paired to control for location, height, and local variability in surrounding
habitat and species diversity. We then identified bat vocalizations on these recordings to
the species level. We documented the presence of five of nine possible bat species over both
roof types: Lasiurus borealis, L. cinereus, L. noctivagans, P. subflavus,andE. fuscus. Of the bat
calls that could be identified to the species level, 66% were from L. borealis. Overall levels
of bat activity were higher over green roofs than over conventional roofs. This study pro-
vides evidence that, in addition to well documented ecosystem benefits, urban green roofs
contribute to urban habitat availability for several North American bat species.
©2015 The Authors. Published by Elsevier B.V. This is an open access article under the CC
BY-NC-ND license ( nd/4.0/).
1. Introduction
Urbanization is a leading cause of species endangerment in the United States (Czech et al., 2000) with persistent trends of
decreased species richness and diversity (McKinney,2008,2002) as well as a high degree of biotic homogenization for most
taxa (Lockwood et al.,2000;McKinney and Lockwood, 1999). As of 2008, more than half the world’s human population
lived in cities, and this proportion is predicted to grow to 72% by 2050 (United Nations, 2012), significantly impacting
biodiversity (Mcdonald et al., 2008). Hence, as the urban human population continues to increase, it becomes progressively
more important to include urbanized areas in biological conservation efforts (Marzluff and Rodewald, 2008). Mitigating
the negative consequences of urbanization, thus conserving biodiversity in urban habitats, has a positive impact on both
humans and ecosystems (Savard et al., 2000). One potential tool in conserving urban biodiversity is the installation of green
Green roofs are vegetated rooftops. Built on flat or sloped rooftops, they consist of a root barrier, a drainage layer, a filter
layer, growing medium, and vegetation (Getter and Rowe, 2006). Green roofs benefit urban ecosystems by providing ser-
vices such as reducing stormwater runoff (Berndtsson,2010;VanWoert et al.,2005) and mitigating the urban heat island
effect (Getter and Rowe, 2006;Smith and Roebber, 2011). More recently, studies have begun to investigate the potential of
green roofs to increase urban biodiversity by providing patches of suitable habitat (Oberndorfer et al., 2007). This may be
Corresponding author. Tel.: +1 443 850 0792.
E-mail address: (K.L. Parkins).
2351-9894/©2015 The Authors. Published by Elsevier B.V. This is an open access article under the CC BY-NC-ND license (
licenses/by-nc- nd/4.0/).
350 K.L. Parkins, J.A. Clark / Global Ecology and Conservation 4 (2015) 349–357
of particular importance in cities where there is more rooftop surface area than available green space. Several recent stud-
ies found that vegetated roofs can provide valuable habitat for a multitude of microorganisms and arthropods, especially
when designed to replicate native habitat (Braaker et al.,2014;Brenneisen,2007;Colla et al.,2009;Getter and Rowe, 2006;
Kadas,2007). Even small green roofs increase the connectivity of urban habitat patches, influencing the diversity of mobile
arthropods positively (Braaker et al., 2014). An arthropod prey base and vegetative cover has the potential to provide us-
able habitat for vertebrates with the mobility to reach rooftops. Birds are known to use green roofs for foraging and nesting
(Baumann, 2007) and, in some cases, green roof habitats are developed specifically for avian species of concern (Gedge and
Kadas, 2005;Oberndorfer et al.,2007).
However, birds are not the only vertebrates with the potential to take advantage of urban rooftop habitats. Bats are an
ecologically and economically important taxonomic group (Boyles et al.,2011;Kunz et al.,2011), and, presumably, volancy
enables them to take advantage of small, elevated patches of habitat that are inaccessible to terrestrial mammals. While
some bats are commonly observed in cities worldwide (e.g., Avila-Flores and Fenton, 2005;Hourigan et al., 2010 and Rydell,
1992), the effects of urbanization are species-specific and highly dependent on landscape context (Gehrt and Chelsvig, 2004,
2003) and level of disturbance (Hourigan et al.,2006;Jung and Kalko, 2011). Most studies of urban bats have found that
urbanization results in a reduction of species diversity and the dominance of a few, open-adapted, generalist species (Avila-
Flores and Fenton, 2005;Coleman and Barclay, 2012;Duchamp and Swihart, 2008;Loeb et al.,2008;Luck et al.,2013;
Threlfall et al.,2011;Ulrey et al.,2005). Even among urban-adapted bats, however, activity is dependent on the availability
of suitable habitat for roosting and foraging as well as prey within the urban matrix (Avila-Flores and Fenton, 2005;Dixon,
2011). Thus, the presence of green roofs with high arthropod abundance and diversity may be beneficial foraging grounds
for bats in urban habitats.
Pearce and Walters (2012) provided preliminary evidence supporting this prediction in the UK: bat activity was higher
over green roofs compared to roofs with only conventional roofing material. Because Pearce and Walters (2012) monitored
each site in their study for only a total of seven nights during a single breeding season and because bat activity has high
temporal variability (Hayes, 1997), their results are difficult to generalize.
The primary objective of this study is to expand the previous research investigating urban green roofs as habitat for bats.
We collected a larger dataset than previous studies by comparing bat activity over urban green and conventional urban
rooftop sites for an entire season. Using passive recording devices, we recorded bat passes and feeding buzzes (defined be-
low), which can indicate foraging activity. We predicted that there would be more bat activity and higher species richness
over urban green roofs than nearby comparable conventional roofs. Because surrounding landscape variables are likely to
influence bat activity at a given site, we also investigated surrounding land cover on overall bat activity.
2. Methods
2.1. Study sites
Study sites were located within the Bronx, Queens, and Manhattan boroughs of New York, NY, USA. New York City (NYC)
has an approximate population of 8.4 million people over 487 km2(US Census Bureau, 2014).
To compare bat activity between green and conventional roof sites, we used a paired study design as recommended by
Hayes (1997) to help control for the large amount of temporal variation in bat activity within and among nights and seasons.
Four green roofs were selected for this study. Each roof had a waterproof membrane and growing substrate, and all were
completely covered in vegetation. For each green roof, a nearby conventional roof site was selected for comparison. Conven-
tional roofs were the same number of stories tall as the paired green roof, were located within one city block of the green
roof, and had conventional blacktop or concrete roofing material with no vegetation (Fig. 1). All paired sites were either six
or eight stories tall and of similar height to surrounding buildings, and there was no difference in lighting on the roofs—no
roofs had distinctive or exceptional nighttime lighting. One of the paired roof sites was connected but located a substantial
distance away from each other so that recorders on each roof type were only recording bat activity over the roof on which
they were installed. Examining recordings after the first week of deployment verified that each set of paired detectors did
not record the same bats simultaneously.
2.2. Bat acoustic recording
Bat activity was recorded using passive SongMeter SM2BAT+(Wildlife Acoustics, Concord, MA) full spectrum ultrasonic
acoustic recording units (detectors) between 1 May and 5 September 2013. Passive sampling was used instead of active
recording because personnel were not allowed on rooftops at night. One detector was deployed in the center of each roof
and left for the duration of the study for a total of eight detectors on eight roofs. We attached external SMX-US omni-
directional microphones to the top of 2.7-m poles to minimize echolocation bounce off of hard surfaces and to maximize
the number and quality of calls recorded. Microphones were calibrated before deployment (Parsons and Szewczak, 2009)
using an Ultrasonic Calibrator (Wildlife Acoustics, Concord, MA) with a 40 kHz pulse.
Detectors were set to record calls continuously from civil twilight to civil twilight. Detectors were set with a 192 kHz
sample rate, 12 kHz digital high pass filter, 18 dB trigger level, microphone bias off, and 36 dB gain. We used a 2.0 s trigger
K.L. Parkins, J.A. Clark / Global Ecology and Conservation 4 (2015) 349–357 351
Fig. 1. Location of paired green and conventional roof sites in New York City, NY, USA used in this study of urban bat activity.
window minimum and 8.0 s maximum file length so that calls would be an appropriate length for the analysis software.
Calls were recorded in WAV format onto data cards and copied to hard drives for later analysis. Data cards and batteries
were changed every two weeks.
2.3. Bat call analysis
Due to occasional unexpected detector failures (e.g., because of battery displacement or vandalism), only data from nights
when both detectors in a pair were functioning for the entire night were included for analysis. This approach helped maintain
the integrity of the paired design. Recordings from all sites were first passed through SonoBat Batch Scrubber Utility 5.2
(DND Design, Arcata, CA) using default settings to remove the majority of files that did not contain bat passes. A bat pass (or
‘‘call’’) was defined as a file with two or more pulses and with each pass separated by one or more seconds (Kalcounis et al.,
1999;White and Ghert, 2001). Due to the large amount of regular, high- and low-frequency ambient noise in our urban
setting, files were then visually inspected on a time–frequency sonogram for the presence of bat echolocation calls in order
to manually eliminate files that contained only non-bat noise.
All passes identified as ‘‘bats’’, including those that were not suitable for species identification, were used to calculate
an index of bat activity. Relative bat activity at each site was quantified as the number of bat passes per night (Gehrt and
Chelsvig, 2003). The activity index does not provide an estimate of abundance of bats in an area (Hayes, 2000) but is, instead,
an estimate of the relative use of a site and can be used to make relative comparisons between sites (Hayes,2000;Parsons
and Szewczak, 2009).
2.3.1. Foraging activity
Quantification of passes containing ‘‘feeding buzzes’’ or ‘‘terminal buzzes’’ (see Griffin, 1958 and Griffin et al., 1960) is
often used to indicate foraging activity in acoustic monitoring studies (e.g., Avila-Flores and Fenton, 2005;Fukui et al., 2006;
Grindal et al., 1999;Kalcounis et al., 1999;McCracken et al., 2007;Pearce and Walters, 2012 and Vaughan et al., 1997). We
examined passes visually for the characteristic high inter-pulse repetition rate, steep pulse slope, and short pulse duration
of a feeding buzz (Griffin et al.,1960;McCracken et al.,2007;Schnitzler and Kalko, 2001) as in Kalcounis et al. (1999). Passes
containing feeding buzzes were labeled as such, tallied for each site, and used to calculate a ‘‘buzz ratio’’ or ratio of feeding
buzzes to bat passes (Vaughan et al., 1996). Passes containing feeding buzzes were only quantified for overall bat activity,
not for each species specifically.
352 K.L. Parkins, J.A. Clark / Global Ecology and Conservation 4 (2015) 349–357
2.3.2. Species identification
Bat passes were examined for quality before species analysis, and only regular, search phase calls with a single echolo-
cating bat were used for species analysis as low-quality, fragmented calls are likely to result in misidentification (Szewczak,
2002). Any obviously fragmented calls were not included for analysis (Miller, 2001). These calls were then analyzed using
default settings in SonoBat NNE 3.2.0 automated classifier: a required call quality of 0.80 and a 0.90 decision threshold (as
in Kalcounis-Ruppell et al., 2013 and Jameson and Willis, 2014). Identifications were then checked using an acoustic identi-
fication key to confirm species presence at each site and to investigate any unusual identifications made by the automated
The ability to make interspecific comparisons among sites using acoustic recordings is limited, and the ability to record
and correctly identify calls varies between species (Hayes,2000;O’Farrell and Gannon, 1999), as species composition can
be skewed by the presence of a small number of highly active bats. To account for species-specific differences in activity, we
used the Miller activity index (Miller, 2001) to examine relative activity between species. The Miller activity index is deter-
mined by the number of one-minute time blocks that each species is present at each site. We also examined the difference
in species richness between sites using only species presence.
2.4. Vegetation cover analysis
Land cover was analyzed using ArcMap10.2 (ESRI, Redlands, CA). The data source was the 2010 Landcover Raster Dataset,
a high resolution (3 ft2) raster available from NYC OpenData ( We reclassified seven land
cover classes into the following four classes: impervious surface (includes road, buildings and other paved surfaces), water,
bare earth, and vegetative cover (includes tree canopy cover and grass/shrubs). We defined concentric circular buffers at
100, 500, and 1000 m around each site (Dixon, 2011) and extracted land cover data from these buffers. Buffers larger than
1000 m could not be used because this resulted in the overlapping of buffers from two of the sites that were only slightly
more than 2 km apart.
2.5. Statistical analysis
All statistical analyses used R version 3.1.1 (R Core Development Team, 2014), and a significance level of α=0.05 was set
for all tests. We used a linear mixed effect model with roof type as a fixed effect and week as the random effect to examine
bat activity over the duration of the sampling period. Differences in proportion of feeding buzzes between roof types and
intraspecific differences in activity were tested using a chi-square test.
We tested for differences in the amount of vegetation at 100, 500, and 1000 m between green and conventional roof
sites using a paired t-test to confirm the integrity of the paired design. We tested for covariance between vegetation at
100, 500, and 1000 m using Pearson’s correlation. Linear regression models were run to examine the relationship between
surrounding vegetation and bat activity.
3. Results
3.1. Overall bat activity
Bat detectors ran for a total of 676 detector nights (where one detector night =one detector deployed at one site for one
night) between 1 May and 5 September 2013. Detectors functioned for an average of 85 nights per site over the sampling
period, and 965 bat passes were recorded. Taking into account the effect of week, the effect of roof type was significant;
green roofs had higher average bat activity per night (F(1,93.25)=4.45 p=0.04) (Fig. 2).
Passes containing feeding buzzes constituted only 2% of all passes, with only 12 and 8 buzzes over green and conventional
roof types respectively. This difference in buzz ratio over green versus conventional roofs was not significant (chi-square
test, p=0.99); however, the number of passes containing feeding buzzes were strongly correlated with total bat passes at
each site (r=0.98,p<0.001).
3.2. Species specific bat activity
Of the 965 total passes, 67% were categorized into the Sonobat designated high frequency call clade, which for the NY
region includes Lasiurus borealis,Perimyotis subflavus, and Myotis spp. The remaining 33% were classified into the low fre-
quency call clade compromising Eptesicus fuscus, Lasionycteris noctivagans, and L. cinereus. Overall, 579 of passes (60%) could
be identified to species.
Over green roofs, five species were recorded with Sonobat estimated likelihoods of 0.90 or above: L. borealis,L.
noctivagans,E. fuscus,P. subflavus and L. cinereus. The most prominent species, L. borealis, accounted for 69% of all identified
passes; 15% were L. cinereus, 15% L. noctivagans, 4% P. subflavus, and 3% E. fuscus.
Over conventional roofs, three species were recorded with Sonobat estimated likelihoods of 0.90 or above: L. borealis,L.
noctivagans, and L. cinereus. There were three passes from P. subflavus and one from E. fuscus, which gave estimated likelihood
K.L. Parkins, J.A. Clark / Global Ecology and Conservation 4 (2015) 349–357 353
Fig. 2. Bat activity index (passes per night) (±SE) over green and conventional roofs in New York City, NY, between 1 May and 5 September 2013. Green
roofs had higher levels of bat activity than conventional roofs (p=0.04). (For interpretation of the references to color in this figure legend, the reader is
referred to the web version of this article.)
Fig. 3. Total activity index (Miller, 2001) for each bat species recorded over green and conventional roofs in New York City, NY, USA: Eptesicus fuscus
(EPFU), Lasiurus borealis (LABO), L. cinereus (LACI), Lasionycteris noctivagans (LANO), Perimyotis subflavus (PESU). Differences in activity were found for only
for EPFU, LABO, and PESU (p<0.05).
values of 0.58 and 0.23 respectively; however, upon inspection and analysis with an acoustic key, all of these passes were
confirmed to be from the species assigned by Sonobat, thus P. subflavus and E. fuscus were also considered confirmed over
conventional roofs. The most prominent species, L. borealis, accounted for 60% of all identified passes; 26.5% were L. cinereus,
11% L. noctivagans, 1% P. subflavus, and 0.5% E. fuscus.
There was no difference in species richness between the roof types: all five species were recorded over both green and
conventional roofs. We found differences between total activity index over each roof type for L. borealis (p<0.001), E. fuscus
(p=0.03), and P. subflavus (p=0.01) (Fig. 3).
354 K.L. Parkins, J.A. Clark / Global Ecology and Conservation 4 (2015) 349–357
Table 1
Vegetation cover at 100, 500, and 1000 m around green and conventional roof
sites (QU =Queens,BX =Bronx,FI =Fashion Institute,GS =Grand St.).
Buffer (m) Site Percent cover
Green roof Conventional roof p-value
100 BX 6.09 5.87
FI 5.70 1.60
GS 3.21 1.03
QU 10.94 10.49
Mean 6.48 4.75 0.27
500 BX 15.80 15.47
FI 10.72 9.28
GS 6.47 4.09
QU 8.26 8.96
Mean 10.31 9.45 0.39
1000 BX 28.2 27.56
FI 15.64 15.51
GS 19.07 18.04
QU 31.86 29.05
Mean 23.69 22.54 0.41
3.3. Surrounding land cover
Surrounding vegetation ranged from 1.0% to 10.9% at 100 m, 4.1% to 15.8% at 500 m, and 15.5% to 31.9% at 1000 m
(Table 1). We found no difference in the amount of surrounding vegetation between green and conventional roofs sites
at any of the three buffer distances (paired t-test, p>0.05). Surrounding vegetation was correlated at 100 and 1000 m
(r=0.82,p=0.01). Bat activity was correlated with surrounding vegetation at 1000 m (r2=0.50,p=0.05).
4. Discussion
4.1. The effect of green roofs
Our prediction that bats would be recorded more often over green than conventional roofs in NYC was based on the
assumption that there would be more arthropod prey available to bats over vegetated roofs; hence, we expected that more
bats would be present over green roofs due to increased foraging activity. Arthropod samples using sticky and bowl traps
collected from three of the four green and conventional roof pairs in this study for a separate research study each showed
higher species richness and abundance of arthropods (D. Partridge, unpublished data). Our initial measure of foraging
activity, the buzz ratio, did not differ between site types, most likely due to an exceptionally low number of passes containing
feeding buzzes recorded. Feeding buzzes are more difficult to record than search phase calls due to faster attenuation of
the feeding buzz over shorter distances (see McCracken et al., 2007), an effect that is likely intensified by the presence of
constant high frequency urban noise. However, the strong correlation between passes containing feeding buzzes and total
passes indicates that total passes may be used as a proxy for foraging activity as in other studies (e.g., Fukui et al., 2006).
The difference in average passes per night between the two roof types was small, but significant, and in agreement with the
results of Pearce and Walters (2012) in the UK. Because we did not record many feeding buzzes, we could not definitively
conclude that bats are foraging over green roofs, and it is possible that they are only commuting in the airspace over the roofs.
However, the significantly greater amount of bat activity over green roofs, combined with evidence of more arthropods on
green roofs, is a likely explanation of increased foraging activity in these patches. The green and conventional roofs in our
study were otherwise similar, and we can think of no other explanation for why bats would choose to commute in green
roof airspace over conventional roof airspace.
The presence of bats at a site does not directly give information on the quality of the site as habitat. Bats may be foraging
over green roofs, but actual prey capture ratios, as well as quality of prey items, are unknown. We also did not compare
between green roofs and other habitat patches, so our conclusions are limited to a comparison of green roofs to conventional
roofs. Green roofs may not perform as well when compared to larger habitat patches or those containing resources other
than just prey, such as water or trees for roosting. There are also other factors that may affect bat activity of both roof types.
The factor ‘‘week’’ included in the analysis shows that bat activity is highly variable and is likely affected by date (seasonal
bat activity) and temperature.
4.2. Surrounding landscape
While we found no difference in surrounding vegetation between the site types, the effect of surrounding vegetation at
1000 m on bat activity regardless of roof type was strong. Even though green roofs had, on average, more bat activity than
conventional roofs, surrounding vegetation explained 50% of bat activity. The roofs with highest activity levels within each
K.L. Parkins, J.A. Clark / Global Ecology and Conservation 4 (2015) 349–357 355
roof type were those with more surrounding green space in the form of trees, shrubs, and grass. This result suggests that the
availability of nearby habitat is important in contributing to the effectiveness of the green roof as a habitat patch. A visual
inspection of aerial photos of the sites reveals that the vast majority of green space near these sites is tree canopy, mostly
in the form of street trees and small parks. Given that the three species recorded most frequently are tree roosting bats – L.
borealis, L. noctivagans, and L. cinereus – the presence of roosting habitat nearby may increase the ability of these species to
utilize the green roof as foraging habitat or the frequency with which they encounter this habitat and subsequently stay to
forage. Another possibility is that, in locations with densely packed buildings and tree canopy, green roofs provide a patch
of open space in which bats can more easily forage. In either case, the combination of green roof and surrounding vegetation
results in the highest bat activity.
4.3. Species-specific effects
While little information is available on the bat community composition in NYC, anecdotal evidence from naturalists and
park employees in NYC, as well as studies on bats in other metropolitan areas in the US (e.g., Loeb et al., 2008 and Kurta
and Teramino, 1992) led us to expect that E. fuscus would be the dominant species recorded during this study. Instead, E.
fuscus was the least recorded of all species, and L. borealis dominated our recordings. It is likely that nearly all of the high
frequency passes recorded (67% of the sample) are from L. borealis. The only other possible high frequency species in the
region are P. subflavus and the Myotis spp. Due to the low numbers of P. subflavus and complete lack of Myotis bats in the
subset of passes that were identified to the species level, the majority of unidentified high frequency passes were probably
L. borealis. Although differences exist in detection rates between bat species that can skew the proportions of species in a
sample, the dominance of L. borealis and low numbers of E. fuscus are substantial enough to challenge conventional wisdom
on the community structure of bats in NYC and warrants further investigation to determine if this pattern holds true in other
areas of NYC or is an artifact of the type of habitats we surveyed (i.e., parks versus building dense areas).
The lack of a difference in the number of recordings of L. noctivagans and L. cinereus over each roof type suggests that
these species were recorded while commuting through the city. The low overall number of passes each for E. fuscus and P.
subflavus suggests that green roofs may not benefit these two species to any great extent. E. fuscus is known to roost in highly
urbanized areas and commute long distances to forage outside the city (Everette et al., 2001), so there is a possibility that
these individuals we recorded are only being recorded over green roofs on their commute to more rural foraging grounds;
however, we would then expect to record E. fuscus near sunset after emergence and again in the early hours of the morning
upon their return. After examining the timing of E. fuscus recordings, we observed no patterns that would indicate that this
is the case; calls from this species were dispersed throughout the night.
The proportion of L. borealis recorded and the greater number of passes recorded over green roofs for this species, sug-
gest that green roofs may be particularly beneficial for this common, generalist species. The peak in activity during the fall
migratory season may be due to increased presence of this species during the migratory period.
5. Conclusions
While we controlled for roof height in this study, green roofs can vary from only a few to tens of stories in height, and
vegetation positioned at certain locations within the three-dimensional space of a city may be more or less beneficial to
bats. Green roofs can also differ in vegetative composition, e.g., from low-lying drought tolerant species to flourishing native
gardens. Our study included representative roofs from both of these classifications. The type of invertebrate habitat a roof’s
vegetation provides likely has an effect on the type and density of prey species available for bats; hence, some green roofs will
provide better foraging habitat than others. There also may be an interaction between activity over green roofs, vegetation
type, date, and temperature. For example, green roofs may be particularly beneficial during the reproductive season or
conversely, during migration. All of these factors deserve additional examination. Further studies that examine the role of
roof height and vegetation type along with recent research on green roof arthropod and avian communities can be used to
inform stakeholders on how best to design green roofs for wildlife habitat. Our study provides a basis for future investigation
of the many factors that may affect bat use of green roofs.
More specifically, our study suggests that bats that reside in urban areas may benefit from the presence of green roofs
over conventional rooftops. Further, green roofs contribute to the diversity and abundance of arthropods in the urban land-
scape and, as such, may be beneficial as both direct foraging grounds and by contributing to prey abundance throughout the
urban landscape. We do not suggest that green roofs be used in lieu of other green spaces but, instead, that they be used in
conjunction with larger green spaces that provide roosts and additional foraging habitat for urban bats. In short, green roofs
have greater potential to benefit bats than conventional roofs.
We thank the following institutions and individuals for access to field sites: Chris and Lisa Goode, Joe Arcoleo, The Fashion
Institute of Technology, Extra Space Storage Inc., Kate Shackford, Matthew Casuccio, Anastasia Cole Plakias, and Brooklyn
Grange Rooftop Farm. Thanks to Dustin Partridge for his input and help with experimental design. We would also like to
thank J.D. Lewis for input on earlier versions of this manuscript.
356 K.L. Parkins, J.A. Clark / Global Ecology and Conservation 4 (2015) 349–357
Avila-Flores, R., Fenton, M.B., 2005. Use of spatial features by foraging insectivorous bats in a large urban landscape. J. Mammal. 86, 1193–1204.
Baumann, N., 2007. Ground-nesting birds on green roofs in Switzerland: Preliminary observations. Urban Habitats 4, 1–14.
Berndtsson, J.C., 2010. Green roof performance towards management of runoff water quantity and quality: A review. Ecol. Eng. 36, 351–360.
Boyles, J.G., Cryan, P.M., McCracken, G.F., Kunz, T.H., 2011. Economic importance of bats in agriculture. Science 332, 41–42.
Braaker, S., Ghazoul, J., Obrist, M.K., Moretti, M., 2014. Habitat connectivity shapes urban arthropod communities: the key role of green roofs. Ecology 95,
Brenneisen, S., 2007. Space for urban wildlife: Designing green roofs as habitats in Switzerland. Urban Habitats 4, 27–36.
Coleman, J.L., Barclay, R.M.R., 2012. Urbanization and the abundance and diversity of Prairie bats. Urban Ecosyst. 15, 87–102.
Colla, S.R., Willis, E., Packer, L., 2009. Can green roofs provide habitat for urban bees (Hymenoptera: Apidae)? Cities Environ. 2, 1–12.
Czech, B., Krausman, P., Devers, P., 2000. Economic associations among causes of species endangerment in the United States. BioScience 50, 593–601.
Dixon, M.D., 2011. Relationship between land cover and insectivorous bat activity in an urban landscape. Urban Ecosyst. 15, 683–695.
1007/s11252-011- 0219-y.
Duchamp, J.E., Swihart, R.K., 2008. Shifts in bat community structure related to evolved traits and features of human-altered landscapes. Landsc. Ecol. 23,
Everette, A.L., OShea, T.J., Ellison, L.E., Stone, L.A., McCance, J.L., 2001. Bat use of a high-plains urban wildlife refuge. Wildl. Soc. Bull. 29, 967–973.
Fukui, D., Murakami, M., Nakano, S., Aoi, T., 2006. Effect of emergent aquatic insects on bat foraging in a riparian forest. J. Anim. Ecol. 75, 1252–1258.
Gedge, D., Kadas, G., 2005. Green roofs and biodiversity. Biologist 52, 1–9.
Gehrt, S.D., Chelsvig, J.E., 2003. Bat activity in an urban landscape: Patterns at the landscape and microhabitat scale. Ecology 13, 939–950.
Gehrt, S.D., Chelsvig, J.E., 2004. Species-specific patterns of bat activity in an urban landscape. Ecology 14, 1–12.
Getter, K.L., Rowe, D.B., 2006. The role of extensive green roofs in sustainable development. HortScience 41, 1276–1285.
Griffin, D.R., 1958. Listening in the Dark. Yale University Press, New Haven, CT.
Griffin, D.R., Webster, F.A., Michael, C.R., 1960. The echolocation of flying insects by bats. Anim. Behav. 8, 141–154.
Grindal, S.D., Morissette, J.L., Brigham, R.M., 1999. Concentration of bat activity in riparian habitats over an elevational gradient. Can. J. Zool. 77, 972–977.
Hayes, J.P., 1997. Temporal variation in activity of bats and the design of echolocation-monitoring studies. J. Mammal. 78, 514–524.
Hayes, J.P., 2000. Assumptions and practical considerations in the design and interpretation of echolocation-monitoring studies. Acta Chiropterol. 2,
Hourigan, C.L., Catterall, C.P., Jones, D., Rhodes, M., 2010. The diversity of insectivorous bat assemblages among habitats within a subtropical urban
landscape. Austral Ecol. 35, 849–857.
Hourigan, C.L., Johnson, C., Robson, S.K.A., 2006. The structure of a micro-bat community in relation to gradients of environmental variation in a tropical
urban area. Urban Ecosyst. 9, 67–82.
Jameson, J.W., Willis, C.K.R., 2014. Activity of tree bats at anthropogenic tall structures: Implications for mortality of bats at wind turbines. Anim. Behav.
97, 145–152.
Jung, K., Kalko, E.K.V., 2011. Adaptability and vulnerability of high flying Neotropical aerial insectivorous bats to urbanization. Divers. Distrib. 17, 262–274.
Kadas, G., 2007. Rare invertebrates colonizing green roofs in London. Urban Habitats 4, 66–86.
Kalcounis, M.C., Hobson, K.A., Brigham, R.M., Hecker, K.R., 1999. Bat activity in the boreal forest: Importance of stand type and vertical strata. J. Mammal.
80, 673–682.
Kalcounis-Ruppell, M.C., Briones, K.M., Homyack, J.A., Petric, R., Marshall, M.M., Miller, D.A., 2013. Hard forest edges act as conduits, not filters, for bats.
Wildl. Soc. Bull. 37, 571–576.
Kunz, T.H., Braun de Torrez, E., Bauer, D., Lobova, T., Fleming, T.H., 2011. Ecosystem services provided by bats. Ann. New York Acad. Sci. 1223, 1–38.
Kurta, A., Teramino, J.A., 1992. Bat community structure in an urban park. Ecography 15, 257–261.
Lockwood, J.L., Brooks, T.M., McKinney, M.L., 2000. Taxonomic homogenization of the global avifauna. Anim. Conserv. 3, 27–35.
Loeb, S.C., Post, C.J., Hall, S.T., 2008. Relationship between urbanization and bat community structure in national parks of the southeastern US. Urban
Ecosyst. 12, 197–214.
Luck, G.W., Smallbone, L., Threlfall, C., Law, B., 2013. Patterns in bat functional guilds across multiple urban centres in south-eastern Australia. Landsc. Ecol.
28, 455–469.
Marzluff, J.M., Rodewald, A.D., 2008. Conserving biodiversity in urbanizing areas: Nontraditional views from a bird’s perspective. Cities Environ. 1, 1–27.
McCracken, G.F., Gillam, E.H., Westbrook, J.K., Lee, Y.F., Jensen, M.L., Balsley, B.B., 2007. Brazilian free-tailed bats (Tadarida brasiliensis: Molossidae, Chiroptera)
at high altitude: links to migratory insect populations. Integr. Comp. Biol. 48, 107–118.
Mcdonald, R.I., Marty, K.L., Forman, R.T.T., 2008. The implications of current and future urbanization for global protected areas and biodiversity
conservation. Biol. Conserv. 141, 1695–1703.
McKinney, M.L., 2002. Urbanization, biodiversity, and conservation. BioScience 52, 883–890.
McKinney, M.L., 2008. Effects of urbanization on species richness: A review of plants and animals. Urban Ecosyst. 11, 161–176.
McKinney, M.L., Lockwood, J.L., 1999. Biotic homogenization: a few winners replacing many losers in the next mass extinction. Science 285, 1834–1836.
Miller, B.W., 2001. A new method for determining relative activity of free flying bats using a new activity index for acoustic monitoring. Acta Chirpoterol.
3, 93–105.
Oberndorfer, E., Lundholm, J., Bass, B., Coffman, R.R., Doshi, H., Dunnett, N., Gaffin, S., Kohler, M., Liu, K.K.Y., Rowe, B., 2007. Green roofs as urban ecosystems:
Ecological structures, functions, and services. BioScience 57, 823–833.
O’Farrell, M.J., Gannon, W.L., 1999. A comparison of acoustic versus capture techniques for the inventory of bats. J. Mammal. 80, 24–30.
Parsons, S., Szewczak, J.M., 2009. Detecting, recording, and analyzing the vocalizations of bats. In: Kunz, T.H., Parsons, S. (Eds.), Ecological and Behavioral
Methods for the Study of Bats. The Johns Hopkins University Press, Baltimore, MD, pp. 91–111.
Pearce, H., Walters, C.L., 2012. Do green roofs provide habitat for bats in urban areas? Acta Chiropterol. 14, 469–478.
R Core Development Team, 2014. R: A language and environment for statistical computing.
Rydell, J., 1992. Exploitation of insects around streetlamps by bats in Sweden. Funct. Ecol. 6, 744–750.
Savard, J.-P.L., Clergeau, P., Mennechez, G., 2000. Biodiversity concepts and urban ecosystems. Landsc. Urban Plann. 48, 131–142.
Schnitzler, H.-U., Kalko, E.K.V., 2001. Echolocation by insect-eating bats. BioScience 51, 557–569.
Smith, K.R., Roebber, P.J., 2011. Green roof mitigation potential for a proxy future climate scenario in Chicago, Illinois. J. Appl. Meteorol. Climatol. 50,
Szewczak, J.M., 2002. Advanced analysis techniques for identifying bat species. In: Brigham, R.M., Kalko, E.K.V., Jones, G., Parsons, S., Limpens, H.J.G.A. (Eds.),
Bat Echolocation Research: Tools, Techniques, Analysis. Bat Conservation International, Austin, TX.
Threlfall, C., Law, B., Penman, T., Banks, P.B., 2011. Ecological processes in urban landscapes: mechanisms influencing the distribution and activity of
insectivorous bats. Ecography 34, 814–826.
Ulrey, W.A., Sparks, D.W., Ritzi, C.M., 2005. Bat communities in highly impacted areas: Comparing Camp Atterbury to the Indianapolis airport. Proc. Indian
Acad. Sci. 114, 73–76.
United Nations, 2012. World urbanization prospects: The 2011 revision. United Nations, Department of Economic and Social Affairs Population Division,
New York, New York, USA.
K.L. Parkins, J.A. Clark / Global Ecology and Conservation 4 (2015) 349–357 357
US Census Bureau, 2014. Annual estimates of the resident population: April 1, 2010 to July 1, 2014—Metropolitan Statistical Area. Available online at: (accessed 15.05.15).
VanWoert, N.D., Rowe, D.B., Andresen, J.A., Rugh, C.L., Fernandez, R.T., Xiao, L., 2005. Green roof stormwater retention. J. Environ. Qual. 34, 1036.
Vaughan, N., Jones, G., Harris, S., 1996. Effects of sewage effluent on the activity of bats (Chiroptera: Vespertilionidae) foraging along rivers. Biol. Conserv.
78, 337–343.
Vaughan, N., Jones, G., Harris, S., 1997. Habitat use by bats (Chiroptera) assessed by means of a broad-band acoustic method. J. Appl. Ecol. 34, 716–730.
White, E.P., Ghert, S.D., 2001. Effects of recording media on echolocation data from broadband bat detectors. Wildl. Soc. Bull. 29, 974–978.
... However, as cities are three-dimensional spaces, areas such as rooftops have until recently been neglected. Green roofs (GR) may potentially provide increased living spaces for vegetation (Vasl and Heim 2016) as well as necessary spaces for organisms to inhabit or migrate (Braaker et al. 2014;Parkins and Clark 2015). Green roofs refer to building roofs which are wholly or partially covered with vegetation/plants and growth medium (Cook-Patton and Bauerle 2012). ...
... Existing studies only explored the influence of the surrounding landscape and arthropod communities on bat activity. It was found that bat activity was positively related to vegetation cover within a 1000 m radius of the roof (Parkins and Clark 2015) as well as moth abundance (Partridge et al. 2020). The seasonal variation in the activity of birds and bats is related to their habits (resident and migratory species) as well as climate (Partridge et al. 2020). ...
... A higher proportion of green space may contain more plant species, which may increase the likelihood of wind or animal mediated seed dispersal to nearby GR (Aloisio et al. 2020). In addition, nearby high quality habitat can increase the utilization of GR by animals (Parkins and Clark 2015) and is important for species that have not yet been able to establish large populations on roofs. However, once they have successfully colonized the roof, the role played by GR characteristics is even greater (Kyro et al. 2018). ...
Full-text available
As a form of green infrastructure, green roofs can enhance urban biodiversity by providing complex vegetation structures, supplying increased foraging and roosting opportunities for animals and increasing habitat connectivity. Although it is widely believed that green roofs can promote urban biodiversity, this idea has not been widely studied on an empirical scale. Therefore, a systematic understanding of the relationship between green roofs and biodiversity from different perspectives is still lacking. Here we provide a systematic review of the empirical literature on the relationship between green roofs and biodiversity. The results suggest that green roofs benefit urban biodiversity to some extent but cannot replace quondam natural habitats or complex artificial greening environments. Additionally, the studies reviewed here focused primarily on the diversity of plants or arthropods and were conducted almost exclusively in the United States and the United Kingdom. Moreover, most studies investigating the factors of green roofs affecting biodiversity focused on roof area, height, age, substrate depth, and plant community. To improve our understanding of the relationship between green roofs and urban biodiversity, more extensive research, particularly in developing countries, as well as more in-depth studies of a greater number of species and taxa, including chordates, mollusks and microbes, from different perspectives (e.g. at the genetic level) and other potential pathways are needed. In the future, the density, distribution pattern, distance and location relationship between different green roofs should be considered in an integrated manner. In order to more effectively support urban biodiversity, green roofs should be used in conjunction with other urban green spaces.
... Wildlife is in decline worldwide (Hallmann et al., 2017;Lister and Garcia, 2018;Rosenberg et al., 2019;Sánchez-Bayo and Wyckhuys, 2019) due, in part, to urbanization (Guenat et al., 2019;Habel et al., 2019;Rosenberg et al., 2019;Sánchez-Bayo and Wyckhuys, 2019). Urban green spaces can help offset urbanization's negative impacts on wildlife; therefore, understanding the ecological drivers of wildlife diversity, a measure of individual abundance and taxonomic richness, in urban green spaces is of particular importance (Oliver et al., 2011;Chiquet et al., 2013;Ferenc et al., 2013;Braaker et al., 2014;Parkins and Clark, 2015;Partridge and Clark, 2018;Forister et al., 2019;Leveau et al., 2019). ...
... Green roofs, roofs covered with an impermeable membrane, growing medium, and vegetation (Oberndorfer et al., 2007), capture stormwater (Gregoire and Clausen, 2011;Abualfaraj et al., 2018), reduce energy use (Santamouris, 2014;Alvizuri et al., 2017;Besir and Cuce, 2018), and can act as an effective tool for increasing wildlife habitat in urban landscapes (Cunningham and Liebezeit, 2015;Parkins and Clark, 2015;Ksiazek-Mikenas et al., 2018;Partridge and Clark, 2018;Dromgold et al., 2020;Partridge et al., 2020). However, most urban green roofs are small in size, isolated from other green spaces, and recently built (Stand and Peck, 2015;Treglia et al., 2018). ...
Full-text available
Global wildlife populations are in decline, in part, due to urbanization. However, in urban landscapes, green infrastructure such as green roofs are being created to provide habitat for wildlife. Green roof isolation, planting heterogeneity, and size can all influence wildlife biodiversity, as may the age of a green roof. When new habitat is created, wildlife use of these new habitats is expected to increase over time. To test this expectation for birds, we monitored bird activity prior to and after installation of small green roof plots on six buildings located within New York City parks. Contrary to expectations, bird activity and bird species richness did not increase after green roof plot installation, nor did they increase over a period of 4 years following installation. These unexpected results may reflect the relatively small size of the plots or the fact that the plots were on buildings located within urban parks. Bird activity and bird species richness varied widely between roofs, and the composition of rooftop bird species may have been more influenced by the characteristics of the surrounding landscapes than the presence of the green roof plots. These findings suggest that small urban green roofs within a larger and, potentially, higher quality habitat may not provide additional habitat for foraging birds. Urban green roofs have numerous ecological and environmental benefits, but the size and characteristics of landscapes surrounding a green roof need to be considered when installing green roofs as wildlife habitat.
... Urban agriculture systems also support pollinator and bird habitats [26]. Green roofs convert underutilized space to provide supportive habitats for various insect species, as well as space for nesting birds, native avian communities, urban wildlife, and pollinators [31,32]. Green roofs have also been shown to provide roosts and foraging habitats for urban bats [32]. ...
... Green roofs convert underutilized space to provide supportive habitats for various insect species, as well as space for nesting birds, native avian communities, urban wildlife, and pollinators [31,32]. Green roofs have also been shown to provide roosts and foraging habitats for urban bats [32]. Green roofs with greater plant diversity and proximity to other green space within the surrounding landscape have also been shown to provide supportive habitats to native bees [33]. ...
Full-text available
Nature-based solutions such as green infrastructure present an opportunity to reduce air pollutant concentrations and greenhouse gas emissions. This paper presents new findings from a controlled field study in Ontario, Canada, evaluating the impact of productive applications of green infrastructure on air pollution and carbon dioxide concentrations across different agricultural morphologies compared to other non-productive applications. This study demonstrates that productive green infrastructure applications are as beneficial as non-productive applications in reducing ozone, nitrogen dioxide, and carbon dioxide concentrations. Nature-based solutions present an opportunity to build climate resilience into agricultural systems through supply-side mitigation and adaptation. The implementation of productive green infrastructure could be a viable agricultural practice to address multiple climate change impacts.
... Similarly, in urban Melbourne, Australia, a positive relationship was observed between vegetation cover within green spaces, abundance of nocturnal invertebrates, and activity and species richness of insectivorous bats [24]. Researchers also speculate that green roofs may provide important foraging spaces for insectivorous bats, since they support more insect populations and bat activity than conventional roofs [25][26][27]. ...
Patches of vegetated habitat within urban areas (“green spaces”) and water bodies (“blue spaces”) are crucial to support urban wildlife, including bats. In this chapter, we review the literature to explore how bats use green and blue spaces, including natural, semi-natural, and manicured vegetated areas, and various water bodies. We first examine the value of urban green spaces to bats for roosting, foraging, commuting, and refuge from disturbances. We then examine the importance of blue spaces as sources of drinking water and prey. We also consider how spatial arrangements of green and blue spaces across the urban landscape influence use by bats. Finally, we review approaches of studying green and blue spaces to guide future research and suggest guidelines for better design and management of these valuable habitats to support urban bat abundance and diversity.KeywordsGreen spaceBlue spaceForagingDrinkingHabitat Urban landscape
... Wildflower green roofs (Fig. 26.1) support pollinators; however, temporal changes in plant cover, due to the periodic senescence of vegetation, could influence citizens' perception (Benvenuti 2014). In addition, green roofs contribute to the diversity and abundance of arthropods in the built environment creating a foraging ground for bats (Parkins and Clark 2015). Arthropod communities on the roofs can vary greatly depending on the diversity of plants, time since construction, and proximity to other habitats (Ksiazek-mikenas et al. 2018). ...
Green infrastructure is an emerging approach to make cities sustainable, healthy and more liveable. Based on a strategically planned network of natural and semi-natural areas in urban, peri-urban and rural landscapes, green infrastructure aims to provide sustainable urban development and to link green and blue spaces at both urban and regional scales. In this study, a green infrastructure design system is anticipated for the city of Antalya. A set of green infrastructure components are identifed and used to delin�eate a system which could take into consideration connections between actual eco�logical hubs, people and nature and past and present. The results show that hubs and lines created by overlapped green infrastructure typologies potentially provide connectivity between city and ecology as well as between people and nature in the city of Antalya, Turkey. Antalya and its urban landscapes have a high potential for a green infrastructure design, but in order to integrate the green infrastructure application into urban planning, a holistic approach will be needed involving municipal, regional and state authorities, local stakehold�ers as well as citizens.
... In addition, health outcomes can be improved by NbS through heat mitigation [62,63,[76][77][78]80,81,86,87]. NbS also support food security by enhancing biodiversity; providing pollinator habitat, and improving soil health [8,63,[88][89][90][91][92][93][94][95][96]. Figure 4 shows the five definitional categories (e.g., infrastructure-related approaches) and general examples (e.g., green infrastructure) of NbS approaches established by the IUCN. ...
Full-text available
This study presents a typology of nature-based solutions (NbS), addressing the need for a standardized source of definitions and nomenclature, and to facilitate communication in this interdisciplinary field of theory and practice. Growing usage of the umbrella phrase ‘nature-based solutions’ has led to a broad inclusion of terms. With the diversity of terminology used, the full potential of NbS may be lost in the confusion of misapplied terms. Standardization and definition of commonly used nature-based nomenclature are necessary to facilitate communication in this rapidly expanding field. Through objective systemization of applications, functions, and benefits, NbS can be embraced as a standard intervention to address societal challenges and support achievement of the UN SDGs.
... Green infrastructure also provides an effective stormwater management solution for water storage during rainfall events, reductions in overland flow, and prevention of sediment erosion and nutrient loading [5,6,66,[81][82][83]. The application of green infrastructure can also enhance biodiversity and provide pollinator habitat [66,[84][85][86][87]. ...
Full-text available
Nature-based solutions (NbS) present an opportunity to reduce rising temperatures and the urban heat island effect. A multi-scale study in Toronto, Ontario, Canada, evaluates the effect of NbS on air and land surface temperature through two field campaigns at the micro and mesoscales, using in situ measurements and LANDSAT imagery. This research demonstrates that the application of NbS in the form of green infrastructure has a beneficial impact on urban climate regimes with measurable reductions in air and land surface temperatures. Broad implementation of green infrastructure is a sustainable solution to improve the urban climate, enhance heat and greenspace equity, and increase resilience.
... This in turn can aid dispersal, increase local biodiversity, and suppress or even reverse population declines (de Araujo and Bernard, 2016;Moretto et al., 2019). These improvements not only benefit bats, but also environmental health and resource availability by facilitating species that undertake essential ecosystem services (Parkins and Clark, 2015). Bats, for example, provide much needed pest control, pollination, and seed dispersal services (Aguiar et al., 2021;Ramirez-Francel et al., 2022). ...
Full-text available
For urban environments to support bat communities, resources need to be readily available. For example, bats typically use urban water sources such as drainage ditches and ponds; however, these sources can be ephemeral. During these periods, bats have utilized residential swimming pools, although they only appear to drink at pools when access to more natural equivalents are limited. This posed the question “can we make residential swimming pools friendlier for a diversity of bat species?” Using citizen science to determine which pool characteristics influenced bat activity, we distributed a questionnaire to residents in a suburban neighborhood in Fort Worth, TX, United States. It focused on observations of bat activity and the features of the pools and immediate surroundings. We distributed the questionnaire through social media, local presentations, and by mail throughout 2019 and 2020. We then used classification trees to determine which characteristics in combination influenced bat activity at the pools. We generated three different trees for bats observed (1) flying around the property and backyard, (2) above the swimming pool, and (3) drinking at the pool. We found that more bats were observed at unlit pools without bush or shrub borders. Furthermore, among pools with borders, activity was lowest at pools with textured interiors and ≥6 trees visible. The presence of features, such as fountains, then contributed to a reduction in bat observations in backyards and the presence of pets appeared to further reduce activity specifically over the pools. Where bats were observed drinking, this activity was reported the least at pools with bush or shrub borders, textured interiors, and trees <5 m and >10 m from the edge of the pools. Our study revealed that certain characteristics of residential swimming pools encouraged bat activity, while others discouraged them. Thus, it may be possible to make swimming pools more bat-friendly. For example, turning lights off in the evening when backyards are not in use and reducing clutter around pools could have an immediate positive impact on local bat populations. The implementation of such recommendations could improve urban habitats for bats overall and alleviate some of the negative implications of continued urbanization.
... Wildflower green roofs ( Fig. 26.1) support pollinators; however, temporal changes in plant cover, due to the periodic senescence of vegetation, could influence citizens' perception (Benvenuti 2014). In addition, green roofs contribute to the diversity and abundance of arthropods in the built environment creating a foraging ground for bats (Parkins and Clark 2015). Arthropod communities on the roofs can vary greatly depending on the diversity of plants, time since construction, and proximity to other habitats (Ksiazek-mikenas et al. 2018). ...
Globally, urbanization has strong impacts on biodiversity, ecological patterns and processes, and ecosystem services. Biodiversity loss due to the rapid expansion of cities and towns may have significant repercussions for human health. However, several studies have reported that increasing and restoring biodiversity in cities can provide several ecosystem services and improve human health and well-being. For instance, higher biodiversity in cities is associated with positive effects on mental health, social cohesion, and crime reduction. In particular, multifunctional green infrastructure, sometimes referred to as blue-green infrastructure, has been effectively used in a variety of ways as a tool to conserve and enhance urban biodiversity efficiently where space is limited. This chapter provides several recommendations for protecting and increasing urban biodiversity through green infrastructure based on ecological design principles. Furthermore, it explores urban green infrastructure case studies, best practices, and policies in the UK and the USA that promote human health, well-being, and biodiversity conservation.
... They are often inaccessible, thus offering an undisturbed habitat. Various species such as birds, spiders, bees and arthropods are observed on green roofs (Fernandez-Canero & Gonzalez-Redondo, 2010;Parkins & Clark, 2015;Williams et al., 2014). However, their richness and abundance are dependent on various factors such as plant diversity, proximity of green roofs to other green roofs or green spaces, height and area of the roof (Mayrand & Clergeau, 2018). ...
Full-text available
Improving biodiversity in urban areas is widely recognised as part of sustainable smart cities development framework. Due to unprecedented urbanisation, there is a lack of adequate green spaces which has in turn affected the urban biodiversity. Green roofs are argued to enhance and support the biodiversity by systematic inclusion into the urban ecological network. However, its connection to the existing natural ecological areas and connectivity are not discussed at a city scale. Thus, in this study, we aim at identifying the connectivity of potential areas for developing green roofs in strengthening the biodiversity and ecological network in cities. Altogether, we observe that the potential roofs are in the near proximity of these zones. The zones with dry lawns and meadows like environment are quite limited and spatially far from each other. Thus, developing green roofs can help in connecting these spaces. In this paper, we mainly focused on bees as they play an important role in pollination and are also declining in the urban areas. Further research can incorporate more detailed analysis on foraging distances of other species. A methodology can be developed to select which zones can be targeted for specific species.
Full-text available
A new activity index for acoustical bat data is presented. The AI (acoustic activity index) was highly correlated to bat passes but proved to be a less biased index of activity. The method dispenses with the need to define, identify and account bat passes and provides a simple means to quantify activity. It uses the Anabat system where acoustic surveys are carried out in real time with the data saved directly to a computer hard drive, taking advantage of the date-time information encoded into each file. The method is based upon the presence/absence of a species occurrence during one-minute time intervals and avoids skewing an index of activity that may reflect the behavior of the species sampled. Examples are given showing that the AI is an effective measure of bat activity allowing comparisons between sites, times and species.
Bat detectors increasingly are used in studies of the ecology and behavior of bats. A number of assumptions are implicit to these studies, although these assumptions rarely are stated explicitly and sometimes are not recognized by researchers. The strength of inference resulting from echolocation-monitoring studies is, in part, a function of the extent to which underlying assumptions are met. Recognition of underlying assumptions is thus an important facet of the design and interpretation of echolocation-monitoring studies. In this paper, I outline and discuss six key assumptions underlying most echolocation-monitoring studies. Accounting for sources of temporal, spatial, and sampling variation is key for designing robust studies and for meeting the assumptions underlying echolocation-monitoring studies.
Biotic homogenization is seen as the consequence of preferential loss of native species followed by ecological replacement with widespread exotics. Homogenization is not random in its effects on higher taxa. Using Monte Carlo simulations (rather than binomial statistics) we find taxonomic patterns in the risk of extinction and probability of successful introduction among birds. Sixteen avian families selectively contain extinct or threatened birds. Eight avian families selectively contain successfully introduced birds. Eight of these 24 taxonomically selected families have not been identified in previous studies, presumably because they are species-poor. The 22 living taxonomically selected families are classified into four homogenization categories. These categories reflect how extinction and invasion are combining in their effects at the family level. Range size, as indexed by island endemism, and human influence are the primary forces driving taxonomic homogenization patterns among birds. There is no evidence that evolutionary age influences homogenization patterns. Phylogenetic comparative analyses, which explicitly recognize the role of human influence, are needed to elucidate more detailed ecological correlates to homogenization trends.
Look down on any town or city from above, and you will see many grey and dreary roofs, there to protect buildings and their occupants from the elements. Imagine, though, if all these roofs were covered in a variety of wild plant species. These forgotten, wasted areas would suddenly become islands of wildlife amidst the hustle and bustle of our cities.
Only the fast-flying bat species that use long-range echolocation systems (Nyctalus noctula, Vespertilio murinus, Eptesicus nilssonii and occasionally Pipistrellus pipistrellus) forage around streetlamps, whereas Myotis spp. and Plecotus auritus did not. Bat density along illuminated roads was 1-5 km-1. Over 90% of the bats detected were E. nilssonii. In and around a small town, E. nilssonii was predominantly found in residential and rural parts, and avoided areas without trees. Vespertilio murinus was observed in all habitats, a difference probably related to differences in the foraging behaviour of the two species. Various lamp types attracted insects in relation to the amount of short wave-lengths emitted. Bats were attracted to the lamp types as insects. The gross energy intake of E. nilssonii foraging around streetlamps was more than twice as high (0.5kJ min-1) as previously recorded in woodlands (0.2kJ min-1) but slightly lower than over pastures where dung beetles occurred (0.6kJ min-1). -from Author