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Differential Responses to Woodland Character and Landscape Context by Cryptic Bats in Urban Environments

  • Paul R. Lintott ,

    p.r.lintott@stir.ac.uk

    Affiliation Biological and Environmental Sciences, School of Natural Sciences, University of Stirling, Stirling, Scotland

  • Nils Bunnefeld,

    Affiliation Biological and Environmental Sciences, School of Natural Sciences, University of Stirling, Stirling, Scotland

  • Jeroen Minderman,

    Affiliation School of Biology, University of St Andrews, St Andrews, Scotland

  • Elisa Fuentes-Montemayor,

    Affiliation Biological and Environmental Sciences, School of Natural Sciences, University of Stirling, Stirling, Scotland

  • Rebekah J. Mayhew,

    Affiliation Biological and Environmental Sciences, School of Natural Sciences, University of Stirling, Stirling, Scotland

  • Lena Olley,

    Affiliation Biological and Environmental Sciences, School of Natural Sciences, University of Stirling, Stirling, Scotland

  • Kirsty J. Park

    Affiliation Biological and Environmental Sciences, School of Natural Sciences, University of Stirling, Stirling, Scotland

Differential Responses to Woodland Character and Landscape Context by Cryptic Bats in Urban Environments

  • Paul R. Lintott, 
  • Nils Bunnefeld, 
  • Jeroen Minderman, 
  • Elisa Fuentes-Montemayor, 
  • Rebekah J. Mayhew, 
  • Lena Olley, 
  • Kirsty J. Park
PLOS
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Abstract

Urbanisation is one of the most dramatic forms of land use change which relatively few species can adapt to. Determining how and why species respond differently to urban habitats is important in predicting future biodiversity loss as urban areas rapidly expand. Understanding how morphological or behavioural traits can influence species adaptability to the built environment may enable us to improve the effectiveness of conservation efforts. Although many bat species are able to exploit human resources, bat species richness generally declines with increasing urbanisation and there is considerable variation in the responses of different bat species to urbanisation. Here, we use acoustic recordings from two cryptic, and largely sympatric European bat species to assess differential responses in their use of fragmented urban woodland and the surrounding urban matrix. There was a high probability of P. pygmaeus activity relative to P. pipistrellus in woodlands with low clutter and understory cover which were surrounded by low levels of built environment. Additionally, the probability of recording P. pygmaeus relative to P. pipistrellus was considerably higher in urban woodland interior or edge habitat in contrast to urban grey or non-wooded green space. These results show differential habitat use occurring between two morphologically similar species; whilst the underlying mechanism for this partitioning is unknown it may be driven by competition avoidance over foraging resources. Their differing response to urbanisation indicates the difficulties involved when attempting to assess how adaptable a species is to urbanisation for conservation purposes.

Introduction

Urbanisation is one of the most dramatic forms of land use change. By 2050 it is expected that 70% of the world’s population will live in urban areas, this expansion will require rapid urban growth which can fragment, destroy or degrade existing natural ecosystems [1]. This can lead to reductions in species richness, diversity, and changes in community composition within the urban landscape (e.g. [2], [3]). We know relatively little about the underlying mechanisms that make certain species adept at adapting to urbanisation which makes the development of management plans to conserve native biodiversity difficult to formulate [4]. Morphological or behavioural factors influence how species respond to the urban landscape, and these traits have been used to classify species as ‘urban avoiders’, ‘urban utilizers’ or ‘urban dwellers’ [5], although in reality there is likely to be a continuous spectrum of adaptability. Understanding where along this spectrum a species lies will help determine the extent of conservation action required.

The prevalence of many species within the urban environment depends on their ability to survive and adapt to heavily modified landscapes and anthropogenic disturbances. In this regard, Chiroptera are one of the few orders of animals in which many species have formed strong associations with human-modified habitats. Human habitations provide roosts, while adaptations of the environment provide food sources, such as ‘light-attracted’ bat species exploiting insect congregations that form at artificial light sources [6]. However, whilst many species have adapted to exploit the urban landscape, the general pattern is of lower bat activity and species richness with increasing levels of urbanisation (e.g. [7], [8], but see [9]). Adaptation to the built environment is highly species-specific, for example species with high mobility (e.g. those with fast, high flight) are often able to utilise habitat patches of high foraging potential in an otherwise unsuitable landscape as their movement is relatively independent from structural features. In contrast, slow flying bats may respond more strongly to small-scale features (e.g. road networks) and therefore their ranging ecology and habitat selection may be more heavily impacted [10]. For example, in the Eastern pipistrelle (Pipistrellus subflavus), the location of foraging sites is influenced more strongly by the distance to hibernacula than the level of urbanisation or degree of woodland fragmentation [11].

Woodland is widely regarded as primary foraging habitat for a range of bat species [12], however urban woodland is of variable quality, subject to invasive species encroachment and often consists of small, fragmented patches [13]. Although management strategies for the conservation of urban woodland are being developed in many countries due to the benefits for human health [14] and biodiversity conservation [15] [16], their effectiveness for the latter is unknown as basic ecological data is lacking for many taxa in urban landscapes. Grouping the conservation requirements of morphologically similar species together would increase the efficiency and effectiveness of management strategies as a greater number of species would benefit from any single conservation action. However, this is problematic if morphologically similar species differ substantially and unpredictably in their response to changes or pressures associated with urbanisation.

In this paper we examine whether closely related species can respond differently to urbanisation. We use two, often sympatric, cryptic species of pipistrelle bat P. pygmaeus and P. pipistrellus which are widespread throughout Europe to investigate how habitat selection within the built environment varies between species. These two species have very similar flight morphologies [17], although they show a small but significant difference in their body size [18] and echolocation call frequencies. Little is known of the response of these cryptic species to the urban landscape although Hale et al. [19] found that P. pipistrellus activity at urban ponds peaked with moderate levels of adjacent urban grey space. Morphological traits are often linked to habitat specialisation and from this the risk of exclusion from highly modified landscapes can be inferred [20]. Consequently, the morphological similarities between P. pipistrellus and P. pygmaeus suggest that both species will respond similarly to the urban matrix. Specifically, we address the following three questions:

  1. Do P. pipistrellus and P. pygmaeus respond similarly to urban woodland vegetation character (e.g. tree density) and patch configuration (woodland size and shape)?
  2. Do P. pipistrellus and P. pygmaeus respond similarly to the composition, spatial configuration, and heterogeneity of the surrounding landscape and, if so, at what spatial extent?
  3. Do P. pipistrellus and P. pygmaeus exhibit similar habitat selection within the urban matrix?
  4. What are the conservation implications of these findings?

Materials and Methods

Ethics Statement

The landowners gave permission for access to all survey sites. All UK bat species are protected and licenses are required if they are to be handled or trapped, however as this study passively monitored their foraging activity there were no licensing issues. The surveying methodology was approved by the Biological and Environmental Sciences ethics committee at the University of Stirling.

Site selection

A total of 31 urban woodlands in central Scotland, UK (Fig 1; Table 1) were identified using Ordnance Survey digital maps [21] and surveyed between May 19th and September 1st 2011. Urban areas were designated as those where urban cover was the dominant land use within a 1 km grid square as categorised by the Centre for Ecology and Hydrology Land Cover Map 2000. Sites were selected by size, longitude, and degree of urbanisation in the surrounding 1 km using a stratified random sampling method. Selected woodlands were a minimum of 50 years old, and were either broadleaved or consisted of a mixture of conifer and broadleaved trees. Sites were surveyed in random order through the field season to avoid any spatial or temporal bias.

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Fig 1. Map of central Scotland showing approximate locations of woodland sites (dark green dots) surveyed in 2011.

Map produced using EDINA Digimap Ordnance Survey Service.

https://doi.org/10.1371/journal.pone.0126850.g001

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Table 1. The latitude and longitude of the 31 urban woodlands surveyed throughout central Scotland in 2011.

https://doi.org/10.1371/journal.pone.0126850.t001

Vegetation surveys

Daytime vegetation surveys were conducted within a week of the bat survey to ensure that appropriate vegetative conditions were recorded. Four circular plots with radii of 20m were randomly located within each woodland patch. At each of the four plots, all trees were counted, identified to at least genus level, and tree basal area measured. Vegetation clutter was measured from 0–4 metres in height at 18 evenly spaced points within each plot to determine vertical forest structure; adopting a similar approach to Smith & Gehrt [22], a four metre pole with sixteen 0.25 subsections marked upon it was placed at each point within the plot. Any foliage, branches, or stems touching a subsection was counted and summed to provide a measure of clutter (100% clutter occurred when foliage touched all points on the pole in each of the 18 points within the plot). Within each plot canopy cover (%) was assessed at 18 points in each plot using a sighting tube with an internal crosshair; if the crosshair intersected canopy vegetation, presence of canopy was recorded. Data for the four vegetation plots were combined to provide a description of each woodland patch. Additionally, the remaining woodland was visually assessed to ensure that the vegetation surveys were representative of the entire woodland patch.

Bat surveys

Woodland stand survey.

Acoustic surveys were used to determine species presence and a measure of relative activity within each woodland patch. Acoustic surveys were undertaken to quantify foraging activity of bats; these are widely used in studies to determine species presence and habitat use for bats (e.g. [23, 24]), and there is evidence that pipistrelle spp. activity correlates positively with density estimates within woodland [25]. Bat activity was quantified using a frequency division bat detector (Anabat SD1, Titley Electronics) fixed on a 1 m high pole with the microphone pointing upwards. The bat detector was placed within the centre of one of the four plots (see section ‘Vegetation surveys’) and rotated between plots every 30 minutes for four hours in total (the length of the shortest night in the study area). Plot locations were ≥ 20 m from the woodland edge, and ≥ 40 m from each other and positioned to avoid paths. All bat recordings were analysed using Analook W [26]. One bat pass was defined as at least two echolocation calls within one second of each other [27, 28]. Both P. pipistrellus and P. pygmaeus can be determined by the characteristic frequency (Fc = the frequency at the right hand end of the flattest portion of a call; [26]) of their search-phase echolocation calls. Bat passes with a Fc of between 49 and 51 kHz were classed as unknown Pipistrellus species.

Urban matrix survey.

Point counts (8 minute duration) were conducted at different locations within and around each woodland patch using a frequency division bat detector (Anabat SD2, Titley Electronics) to compare differences in P. pipistrellus and P. pygmaeus activity at the woodland interior, edge, surrounding green space, and grey space. Grey space was categorised as land that is sealed, impermeable ‘hard’ surfaces such as tarmac or concrete (e.g. car parks, urban housing), whilst unsealed, permeable ‘soft’ surfaces such as soil and grass were classed as non-wooded green space (e.g. parkland, amenity grassland; following [29]). Three point counts were conducted within each habitat (a total of 12 point counts per night). These were conducted simultaneously to the woodland stand survey and recordings were analysed in the same manner.

Landscape analysis

Bat detector locations were plotted using ArcGIS 10 [30] and the centre point of the four plots within each site determined. Buffers of 250 m, 500 m, 1000 m, 1500 m, 2000 m, 2500 m and 3000m radius were created around the central point. We selected these different scales because the smallest represents site-specific characteristics, the intermediate scales have previously been found to be important predictors of pipistrelle spp. activity within human-disturbed landscapes [31], and the largest scale reflects the upper limit of home range size for P. pygmaeus and P. pipistrellus [32]. Data from the OS MasterMap Topography Layer [21] was used to reclassify the landscape within each buffer into a set of discrete biotope types. These were (i) greyspace (buildings, structures, roads, and paths); (ii) green space (gardens, parkland, managed grassland, rough grassland, and farmland); (iii) inland fresh water and (iv) woodland (coniferous, deciduous and mixed woodland). Woodland Euclidean nearest neighbour distance (ENN, the mean value of ENN distances between all woodland patches within the landscape) and the Shannon diversity index (SHDI, a measure of landscape heterogeneity) were calculated as previous studies have found these variables to influence bat foraging activity [24]. The proportion of land covered by each biotope, woodland ENN, and SHDI were calculated for each buffer scale using Fragstats v4.0 [33].

Data analysis

Statistical analyses were undertaken using R version 2.14 [34] using the lme4 [35] and effects package [36].

Woodland stand survey

We performed a Generalised Linear Mixed-Effects model (GLMMs; [37]) with binomial error distribution and a logit link to quantify the influence of woodland characteristics and landscape metrics on P. pipistrellus and P. pygmaeus activity. In order to assess the relative effects of these variables on P. pygmaeus in comparison to P. pipistrellus, the model was run with the proportion of P. pygmaeus to P. pipistrellus passes per plot (n = 124) as the response variable, with ‘site’ (woodland) included as a random (grouping) factor (n = 31) to account for pseudoreplication of multiple recordings per site [37, 38]. Based upon the scientific literature on the ecology of woodland bats (e.g. [24]) the following predictor variables were included in the model: (i) woodland vegetation characteristics: tree species richness, average tree basal area, woodland clutter and woodland canopy cover (covariates) and woodland type as a fixed factor; (ii) patch configuration: woodland size, woodland shape (covariates), and the interaction between size and shape. Woodland shape is the perimeter divided by the minimum perimeter possible for a maximally compact patch of the same area. This equals 1 when the patch is maximally compact and increases as shape becomes irregular [33]; (iii) landscape metrics (covariates). Temperature and date were also included in all models as covariates. Given the high collinearity found between landscape metrics (i.e. between the proportions of different biotope types or the same biotope type at a variety of spatial scales) preliminary analyses were conducted to determine which landscape metrics should be included in the model. We used GLMMs for the proportion of P. pygmaeus to P. pipistrellus passes per plot with single landscape parameters (at each spatial scale) as a preliminary assessment of which key landscape predictors should be included in the final model (i.e. highest R2 value). If several landscape parameters were of equal importance (i.e. <5% difference between the highest R2 value) they were all selected, providing they were not strongly correlated.

We present the result of the full model including standardised parameters and confidence intervals for all explanatory variables. Inferences on the effect of each parameter were made by (i) comparing its standardized estimate with other predictor variables to determine relative importance, (ii) the upper and lower 95% quantiles of each parameter distribution obtained from N = 2000 simulated draws from the estimated distribution [39], and (iii) a comparison of models excluding each parameter in turn using Likelihood Ratio Tests (LRTs) [40]. LRTs of main effect parameters also involved in interactions were performed by comparing a model excluding the main effect term to a model including all main effects (but not interactions) only. Prediction plots were constructed by undertaking simulated draws (n = 2000) from the estimated distribution of one explanatory variable whilst maintaining all other parameters in the model at their median observed values.

Urban matrix survey

Generalised Linear Mixed-effects Models with a binomial distribution were conducted to assess differences in bat activity between habitats within the urban matrix (n = 93 per habitat); woodland interior, woodland edge, urban green space, and urban grey space. The probability of recording P. pygmaeus (relative to recording P. pipistrellus) within each point count location was included as the response variable. Habitat (e.g. woodland interior) was included in the model as a fixed factor, whereas ‘site’ was used as a random factor (to account for pseudoreplication within sites). Date and temperature were included as covariates.

Results

Woodland stand survey

We recorded a total of 2,364 bat passes during a total of 124 hours of surveys. Bats were recorded within all but one of the 31 woodlands surveyed. We recorded a total of 1,584 P. pygmaeus passes (67% of all bat passes) in 28 of the woodlands, and 642 (27%) P. pipistrellus passes in 23 woodlands. A further 68 pipistrelle passes were recorded however these could not be classified to species level. Additionally, we recorded 69 Myotis spp. bat passes within seven woodlands and one P. nathusii pass. Both of these taxa were found in an insufficient number of sites for robust statistical analysis and were therefore excluded from further analysis.

In the results described below it should be noted that significant variables derived from the bat GLMMs indicate a differential response between the species to site or landscape characteristics; variables which are similarly influential for both species will not therefore be statistically significant in these models. Preliminary landscape analysis identified the proportion of grey space in the surrounding 3 km as the key landscape predictor (i.e. highest R2 value; Fig 2) which was then incorporated into the final model.

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Fig 2. Differential responses to the urban landscape at a variety of spatial scales by cryptic bat species.

R2 values obtained from GLMM models with binomial error distribution comparing the percentage of landscape covered by each biotype type at a variety of spatial scales to the probability of recording P. pygmaeus relative to P. pipistrellus in fragmented urban woodland. The position of the R2 values along the y-axis reflect the direction of the parameter estimates; hence R2 values in the upper half of the graph refer to a landscape metric that is associated with an increased probability of detecting P. pygmaeus, whilst R2 values in the lower half of the graph refer to a landscape metric that is associated with an increased probability of detecting P. pipistrellus.

https://doi.org/10.1371/journal.pone.0126850.g002

The importance of woodland vegetation characteristics and the surrounding landscape differed between P. pygmaeus and P. pipistrellus (Table 2). The proportion of grey space in the surrounding 3 km had the largest effect size and a negative influence on the probability of recording P. pygmaeus relative to P. pipistrellus. Based on the estimated coefficients in Table 2, the predicted probability of recording P. pygmaeus was 0.93 (0.91–0.95) in woodlands surrounded by only a low proportion (10%) of grey space, whilst there was an equal probability of recording either P. pygmaeus or P. pipistrellus in woodlands surrounded by moderate levels of grey space (30%; Fig 3A). In woodlands surrounded by high levels of grey space (45%), the predicted probability of recording P. pygmaeus relative to P. pipistrellus was 0.17 (0.12–0.25). Woodland clutter had the largest effect size of the vegetation characteristics we assessed. There was a high probability of recording P. pygmaeus in woodlands with low (10%) clutter (0.86; 0.82–0.89), whilst in densely cluttered woodlands (40%) the probability of recording P. pygmaeus relative to recording P. pipistrellus fell to 0.37 (0.26–0.50; Fig 3B). Similarly, the probability of recording P. pygmaeus in woodlands with low understory cover (20%) was 0.89 (0.85–0.92), whilst in woodlands with continuous understory cover (100%) there was a similar probability of recording either P. pygmaeus (0.55; 0.49–0.61) or P. pipistrellus (0.45; 0.39–0.51; Fig 3C). Additionally the probability of P. pygmaeus decreased in woodlands with a high average tree basal area, however the effect size was relatively small (Table 2).

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Fig 3. Differential responses to urban woodland and the surrounding landscape by cryptic bat species.

Estimated probability of recording P. pygmaeus relative to P. pipistrellus in fragmented urban woodland. Dashed lines indicate 95% confidence intervals. Original data on the proportion of P. pygmaeus passes are superimposed as grey circles with diameter proportion to the total number of P. pygmaeus passes recorded.

https://doi.org/10.1371/journal.pone.0126850.g003

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Table 2. Parameter estimates and likelihood ratio tests of the GLMM for the relative proportion of P. pygmaeus passes to P.pipistrellus passes in urban woodland.

https://doi.org/10.1371/journal.pone.0126850.t002

Urban matrix survey

We recorded a total of 260 P. pipistrellus passes and 701 P. pygmaeus passes within the four habitat types. The probability of recording P. pygmaeus relative to recording P. pipistrellus was significantly associated with habitat type (χ2 = 20.57, df = 3, p<0.001), and was substantially higher in woodland (interior and edge) than the surrounding urban matrix (Fig 4). There was no substantial difference in the probability of recording P. pygmaeus (relative to P. pipistrellus) between urban green space and non-wooded grey space (Fig 4).

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Fig 4. Differential habitat use in the urban matrix by cryptic bat species.

Boxplot showing the estimated probability of recording P. pygmaeus relative to recording P.pipistrellus in the urban matrix. The upper and lower whiskers show 95% confidence limits. Fitted values by GLMMs are used.

https://doi.org/10.1371/journal.pone.0126850.g004

Discussion

Determining the ecological and behavioural mechanisms driving habitat use within the urban matrix is the key to understanding the adaptability of species to urbanisation. In this study we show that even two morphologically similar species can have widely differing responses to fragmented urban woodland and the surrounding urban matrix.

The response of P. pipistrellus and P. pygmaeus to urban woodland vegetation character and patch configuration

Although habitat partitioning between P. pipistrellus and P. pygmaeus is known from radio tracking studies (e.g. [41]), these studies have involved relatively small sample sizes and were conducted in non-urban habitats. Whilst previous studies have indicated that habitat partitioning between the two species occurs between habitat types (e.g. [42]), here we show that similar behaviour occurs within habitat types, at a fine spatial scale.

Our results indicate that P. pygmaeus appear to be using woodlands with low clutter and understory growth relatively more intensely than P. pipistrellus, despite both species having similar wing shapes and echolocation calls which make them well adapted to foraging along woodland edges and relatively open habitats [43]. These findings support Davidson-Watts & Jones [42] who found that P. pygmaeus spend less time flying, make fewer foraging bouts but travel greater distances, suggesting that this species has more selective foraging habitats. Conversely, P. pipistrellus is commonly regarded as a generalist forager [42, 44], and therefore would be expected to be found in a wider range of habitat types. Although it is surprising that P. pipistrellus are not also using less cluttered habitats, Nicholls and Racey [41] suggested that P. pipistrellus actively avoid P. pygmaeus foraging sites (but see [45]). Coexisting species must differ in at least one niche dimension to avoid excessive competition such as using different foraging locations [46]. It is therefore possible that the use of woodlands with high clutter and understory by P. pipistrellus may reflect the wider, non-selective, use of woodland habitats within the urban matrix to avoid competition. In contrast, P. pygmaeus may be preferentially selecting those woodlands which offer optimal foraging locations. Pipistrellus species are known to also forage above the canopy of closed mature woodland stands [47] which although not recorded in this study, may provide additional or alternative foraging resources for either or both Pipistrellus species. Differences in habitat use may also reflect that the diets of the two species differ [48]. Assessing which woodland characteristics determine prey availability may also help explain differential habitat use.

The response of P. pipistrellus and P. pygmaeus to the composition, spatial configuration, and heterogeneity of the surrounding landscape

Regardless of the spatial scale surrounding the woodland (250 m to 3 km) we found that the probability of recording P. pygmaeus relative to P. pipistrellus was greater when the landscape contained a high proportion of woodland and a low proportion of urban grey space. This supports previous studies identifying P. pipistrellus as a generalist species [32, 49] which can tolerate moderate levels of urbanisation [19]. Similarly, the proportion of grey space in the surrounding 3 km was the strongest predictor of which of the two species would be recorded. The underlying cause as to why P. pipistrellus is better able to adapt to the urban landscape is unknown although the lower frequency of its echolocation call may aid adaptability to cities as species with lower calls are better able to use open habitats and access a wider spectrum of habitats [50]. Alternatively, P. pipistrellus may have the greater behavioural capacity to adapt to exploit the urban landscape, for example using buildings and planted tree lines as paths for courtship flights and territory boundaries [51]. It is surprising given the strong association between P. pygmaeus habitat preferences and waterbodies [44] that the composition of water in the landscape was not a significant predictor of differences in habitat use between the two species. However, urban waterways are frequently used by both species (Lintott et al. unpublished data) and it is likely that the continuous nature of urban waterways is facilitating the movement of both species through the urban matrix. Additionally, in contrast to alternative biotope types (e.g. green space or grey space) there was relatively little variability between sites in the composition of freshwater in the surrounding landscape (S1 Table), which may have masked any differing habitat use as consequence of freshwater.

Differences between P. pipistrellus and P. pygmaeus in habitat selection within the urban matrix

The higher adaptability to the built landscape by P. pipistrellus relative to P. pygmaeus is further supported by the extent to which this species was recorded in a variety of habitat types contained within the urban matrix. In contrast, P. pygmaeus, relative to P. pipistrellus, predominantly used woodland edge and interior habitats; foraging locations that both species are well adapted for. This strengthens Nicholls and Racey’s [41] findings that P. pipistrellus appear to actively avoid P. pygmaeus foraging sites resulting in differential habitat use. Within the urban matrix, this may transpire as P. pipistrellus appearing to using a wider range of habitats, thereby giving the impression that it is a generalist. Similarly P. pipistrellus may be commuting further to use those woodlands which offer suitable foraging resources but are surrounded by sufficient grey space to deter P. pygmaeus.

Conservation implications

Understanding how species respond to urbanisation is critical in identifying priority species which may require conservation effort. Categorising species as either ‘urban avoiders’, ‘urban utilizers’ or ‘urban dwellers’ appears a convenient way of achieving this [5]. Bats are often categorised in this manner based upon their morphological traits (e.g. [50, 52]), however our results show that habitat use differs between species which are morphologically very similar [53, 54] suggesting that such differences may be a weak indication of ecological differences between taxa [41, 55]. Similarly, using species presence as an indication of adaptability to the built landscape should be treated cautiously prior to assessing if adaptability to urbanisation is sex dependent [56], or if species in urban landscapes largely consist of sink populations. If P. pipistrellus are using the urban ecosystem as a means of avoiding competition with P. pygmaeus it may be that they are not so much exploiting the urban landscape but using it out of necessity.

Conclusions

The complexity of understanding species-specific responses to urbanisation makes identifying priority species for conservation action difficult. Here, we show that attempts to use morphological traits as a means of categorising species into the likelihood of them adapting to urban locations are problematic, as even two sympatric and cryptic species can respond differently. P. pygmaeus appear to be using less cluttered woodlands whilst P. pipistrellus appear to be adapting a generalist foraging behaviour using, often cluttered, woodlands surrounded by relatively high levels of urban grey space; this may be a result of differential habitat use to avoid competition.

Supporting Information

S1 Table. The composition of the landscape surrounding the 31 urban woodlands surveyed throughout central Scotland in 2011.

https://doi.org/10.1371/journal.pone.0126850.s001

(DOCX)

Acknowledgments

This project was funded by the University of Stirling and British Ecological Society. We would like to thank Catherine Gibson-Poole, Lorna Blackmore and the numerous volunteers who helped with the data collection. We also thank the two anonymous reviewers for their valuable comments on the manuscript.

Author Contributions

Conceived and designed the experiments: PRL KJP EFM. Performed the experiments: PRL RJM LO. Analyzed the data: PRL NB JM. Wrote the paper: PRL KJP NB JM EFM.

References

  1. 1. Zipperer WC, Pickett STA. Urban Ecology: patterns of population growth and ecological effects. John Wiley & Sons Ltd; 2012.
  2. 2. McKinney ML. Effects of urbanization on species richness: a review of plants and animals. Urban Ecosyst. 2008; 11: 161–176.
  3. 3. Grimm NB, Faeth SH, Golubiewski NE, Redman CL, Wu J, Bai X, et al. Global change and the ecology of cities. Science. 2008; 319: 756–760. pmid:18258902
  4. 4. Magle SB, Hunt VM, Vernon M, Crooks KR. Urban wildlife research: past, present, and future. Biol Cons. 2012; 155: 23–32.
  5. 5. Fischer JD, Schneider SC, Ahlers AA, Miller JR. Categorizing wildlife responses to urbanization and conservation implications of terminology. Conserv. Biol. 2015;
  6. 6. Mathews F, Roche N, Aughney T, Jones N, Day J, Baker J, et al. Barriers and benefits: implications of artificial night-lighting for the distribution of common bats in Britain and Ireland. Proc. R. Soc. B. 2015; 370: 20140124.
  7. 7. Gaisler J, Zukal J, Rehak Z, Homolka M. Habitat preference and flight activity of bats in a city. J. Zool. 1998; 244: 439–445.
  8. 8. Lane DJ, Kingston T, Lee BPH. Dramatic decline in bat species richness in Singapore, with implications for Southeast Asia. Biol Cons. 2006; 131: 584–593.
  9. 9. Gehrt SD, Chelsvig JE. Bat activity in an urban landscape: patterns at the landscape and microhabitat scale. Ecol Appl. 2003; 13: 939–950.
  10. 10. Russo D, Ancillotto L. Sensitivity of bats to urbanization: A review. Z Saugetierkd. 2014; “In press”.
  11. 11. Johnson JB, Gates JE, Ford WM. Distribution and activity of bats at local and landscape scales within a rural—urban gradient. Urban Ecosyst. 2008; 11: 227–242.
  12. 12. Lacki MJ, Hayes JP, Kurta A. (Eds.) Bats in Forests: Conservation and Management. The Johns Hopkins University Press, Baltimore; 2007.
  13. 13. Alvey AA. Promoting and preserving biodiversity in the urban forest. Urban For. Urban Greening. 2006; 5: 195–201.
  14. 14. Matsuoka RH, Kaplan R. People needs in the urban landscape: analysis of landscape and urban planning contributions. Landsc. Urban Plan. 2008; 84: 7–19.
  15. 15. Cornelis J, Hermy M. Biodiversity relationships in urban and suburban parks in Flanders. Landsc. Urban Plan. 2004; 69: 385–401.
  16. 16. Croci S, Butet A, Georges A, Aguejdad R, Clergeau P. Small urban woodlands as biodiversity conservation hot-spot: a multi-taxon approach. Landscape Ecol. 2008; 23: 1171–1186.
  17. 17. Jones G, Van Parijs SM. Bimodal echolocation in pipistrelle bats: are cryptic species present? Proc. R. Soc. B. 1993; 251: 119–125. pmid:8096079
  18. 18. Barlow KE, Jones G. Roosts, echolocation calls and wing morphology of two phonic types of Pipistrellus pipistrellus. Z Saugetierkd. 1999; 64: 257–268.
  19. 19. Hale JD, Fairbrass AJ, Matthews TJ, Sadler JP. Habitat composition and connectivity predicts bat presence and activity at foraging sites in a large UK conurbation. PloS one. 2012; 7: e33300. pmid:22428015
  20. 20. Safi K, Kerth G. A comparative analysis of specialization and extinction risk in temperate—zone bats. Conserv. Biol. 2004; 18: 1293–1303.
  21. 21. EDINA Digimap Ordnance Survey Service, OS MasterMap Topography Layer. 2014. Available: http://edina.ac.uk/digimap.
  22. 22. Smith DA, Gehrt SD. Bat response to woodland restoration within urban forest fragments. Restoration Ecol. 2010; 18: 914–923.
  23. 23. Roche N, Langton S, Aughney T, Russ JM, Marnell F, Lynn D, et al. A car-based monitoring method reveals new information on bat populations and distributions in Ireland. Anim. Conserv. 2011; 14: 642–651.
  24. 24. Fuentes-Montemayor E, Goulson D, Cavin L, Wallace JM, Park K. Fragmented woodlands in agricultural landscapes: The influence of woodland character and landscape context on bats and their insect prey, Agric. Ecosyst. Environ. 2013; 172: 6–15.
  25. 25. Lintott PR, Fuentes-Montemayor E, Goulson D, Park KJ. Testing the effectiveness of surveying techniques in determining bat community composition within woodland. Wildlife Res. 2014; 40: 675–684
  26. 26. Corben C. AnalookW for bat call analysis using ZCA version 3.3f. 2006. Available: http://www.hoarybat.com.
  27. 27. Fenton MB. A technique for monitoring bat activity with results obtained from different environments in southern Ontario. Can J Zool. 1970; 48: 847–851.
  28. 28. Walsh AL, Harris S. Foraging habitat preferences of vespertilionid bats in Britain. J Appl Ecol. 1996; 33: 508–518.
  29. 29. James P, Tzoulas K, Adams MD, Barber A, Box J, Breuste J, et al. Towards an integrated understanding of green space in the European built environment. Urban For. Urban Greening. 2009; 8: 65–75.
  30. 30. ESRI Inc. ArcGIS 10. 2014. Available: http://www.esri.com.
  31. 31. Fuentes-Montemayor E, Goulson D, Park KJ. Pipistrelle bats and their prey do not benefit from four widely applied agri-environment management prescriptions. Biol Cons. 2011; 144: 2233–2246.
  32. 32. Nicholls B, Racey PA. Contrasting home-range size and spatial partitioning in cryptic and sympatric pipistrelle bats. Behav. Ecol. Sociobiol. 2006; 61: 131–142.
  33. 33. McGarigal K, Cushman SA, Neel MC, Ene E. FRAGSTATS: Spatial PatternAnalysis Program for Categorical Maps. University of Massachusetts, Amherst; 2002.
  34. 34. R Core Team. R: A Language and Environment for Statistical Computing. R Foundation for Statistical Computing, Vienna, Austria. 2012. ISBN 3-900051-07-0. https://doi.org/10.1002/jcc.22917 pmid:22278855
  35. 35. Bates D, Maechler M, Bolker B. lme4: Linear mixed-effects models using S4 classes. R package version 0.999999–2; 2013.
  36. 36. Fox J. Effect displays in R for generalised linear models. J Stat Softw. 2003; 8: 1–27.
  37. 37. Zuur A, Ieno EN, Walker N, Saveliev AA, Smith GM. Mixed effects models and extensions in ecology with R. Springer Science & Business Media; 2009.
  38. 38. Pinheiro JC, Bates DM. Mixed effects models in S and S-PLUS. Springer Science & Business Media; 2000.
  39. 39. Gelman A, Hill J. Data analysis using regression and multilevel/hierarchical models. Cambridge: Cambridge University Press; 2007.
  40. 40. Faraway JJ. Extending the linear model with R: generalized linear, mixed effects and nonparametric regression models. New York: CRC press; 2005.
  41. 41. Nicholls B, Racey PA. Habitat selection as a mechanism of resource partitioning in two cryptic bat species Pipistrellus pipistrellus and Pipistrellus pygmaeus. Ecography. 2006; 29: 697–708.
  42. 42. Davidson-Watts I, Jones G. Differences in foraging behaviour between Pipistrellus pipistrellus (Schreber, 1774) and Pipistrellus pygmaeus (Leach, 1825). J. Zool. 2006; 268: 55–62.
  43. 43. Kalko EK, Schnitzler HU. Plasticity in echolocation signals of European pipistrelle bats in search flight: implications for habitat use and prey detection. Behav. Ecol. Sociobiol. 1993; 33: 415–428.
  44. 44. Russ JM, Montgomery WI. Habitat associations of bats in Northern Ireland: implications for conservation. Biol Cons. 2002; 108: 48–58.
  45. 45. Barlow KE, Jones G. Function of pipistrelle social calls: field data and a playback experiment. Anim. Behav. 1997; 53: 991–999.
  46. 46. Li Y, Wang J, Metzner W, Luo B, Jiang T, Yang S, et al. Behavioral responses to echolocation calls from sympatric heterospecific bats: implications for interspecific competition. Behav. Ecol. Sociobiol. 2014; 68: 657–667.
  47. 47. Müller J, Brandl R, Buchner J, Pretzsch H, Seifert S, Strätz C, et al. From ground to above canopy—Bat activity in mature forests is driven by vegetation density and height. For. Ecol. Manage. 2013; 306: 179–184.
  48. 48. Barlow KE. The diets of two phonic types of the bat Pipistrellus pipistrellus in Britain. J. Zool. 1997; 243: 597–609.
  49. 49. Vaughan N, Jones G, Harris S. Habitat use by bats (Chiroptera) assessed by means of a broad-band acoustic method. J Appl Ecol. 1997; 34: 716–730.
  50. 50. Threlfall CG, Law B, Banks PB. Sensitivity of insectivorous bats to urbanization: implications for suburban conservation planning. Biol Cons. 2012; 146: 41–52.
  51. 51. Sachteleben J, von Helversen O. Songflight behaviour and mating system of the pipistrelle bat (Pipistrellus pipistrellus) in an urban habitat. Acta Chiropterologica. 2006; 8: 391–401.
  52. 52. Jung K, Kalko EK. Adaptability and vulnerability of high flying Neotropical aerial insectivorous bats to urbanization. Divers. Distrib. 2011; 17: 262–274.
  53. 53. Barlow KE, Jones G, Barratt EM. Can skull morphology be used to predict ecological relationships between bat species? A test using two cryptic species of pipistrelle. Proc. R. Soc. B. 1997; 264: 1695–1700. pmid:9404031
  54. 54. Häussler U, Nagel A, Braun M, Arnold A. External characters discriminating sibling species of European pipistrelles, Pipistrellus pipistrellus (Schreber, 1774) and P. pygmaeus (Leach, 1825). Myotis. 1999; 37: 27–40.
  55. 55. Davidson-Watts I, Walls S, Jones G. Differential habitat selection by Pipistrellus pipistrellus and Pipistrellus pygmaeus identifies distinct conservation needs for cryptic species of echolocating bats. Biol Cons. 2006; 133: 118–127.
  56. 56. Lintott PR, Bunnefeld N, Fuentes-Montemayor E, Minderman J, Park KJ. City life makes females fussy: sex differences in habitat use of temperate bats in urban areas. Royal Society Open Science. 2014; 1: 140200.