Traffic disturbances (i.e. pollution, light, noise, and vibrations) often extend into the area surrounding a road creating a ‘road-effect zone’. Habitat within the road-effect zone is degraded or, in severe cases, completely unsuitable for wildlife, resulting in indirect habitat loss. This can have a disproportionate impact on wildlife in highly modified landscapes, where remaining habitat is scarce or occurs predominantly along roadside reserves. In this study, we investigated the road-effect zone for insectivorous bats in highly cleared agricultural landscapes by quantifying the change in call activity with proximity to three major freeways. The activity of seven out of 10 species of bat significantly decreased with proximity to the freeway. We defined the road-effect zone to be the proximity at which call activity declined by at least 20% relative to the maximum detected activity. The overall road-effect zone for bats in this region was 307 m, varying between 123 and 890 m for individual species. Given that this road-effect zone exceeds the typical width of the roadside verges (<50 m), it is possible that much of the vegetation adjacent to freeways in this and similar landscapes provides low-quality habitat for bats. Without accounting for the road-effect zone, the amount of habitat lost or degraded due to roads is underestimated, potentially resulting in the loss of wildlife, ecosystem services and key ecosystem processes (e.g. predator-prey or plant-pollinator interactions) from the landscape. We suggest all future environmental impact assessments include quantifying the road-effect zone for sensitive wildlife, in order to best plan and mitigate the impact of roads on the environment. Mitigating the effects of new and existing roads on wildlife is essential to ensure enough high-quality habitat persists to maintain wildlife populations.
Citation: Bhardwaj M, Soanes K, Lahoz-Monfort JJ, Lumsden LF, van der Ree R (2021) Insectivorous bats are less active near freeways. PLoS ONE 16(3): e0247400. https://doi.org/10.1371/journal.pone.0247400
Editor: Andrés Viña, Michigan State University, UNITED STATES
Received: July 21, 2020; Accepted: February 5, 2021; Published: March 10, 2021
Copyright: © 2021 Bhardwaj et al. This is an open access article distributed under the terms of the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original author and source are credited.
Data Availability: Data is available at doi: 10.6084/m9.figshare.12681464.
Funding: Funding for this study was provided by The Baker Foundation (RvdR), Earthwatch Institute (RvdR), Holsworth Wildlife Research Endowment (MB), and the Albert Shimmins Fund (MB). KS is supported by the Clean Air and Urban Landscapes Hub and Threatened Species Recovery Hub of the Australian Government’s National Environmental Science Program. The funders had no role in study design, data collection and analysis, decision to publish, or preparation of the manuscript.
Competing interests: The authors have declared that no competing interests exist. WSP, current affiliation for Rodney van der Ree, played no role in this study and did not provide any funding or salary at the time of the study. This does not alter our adherence to PLOS ONE policies on sharing data and materials.
Roads and traffic are prominent features of most landscapes  and can have numerous negative impacts on wildlife, such as road mortality, barrier effects, and habitat loss and degradation [2–5]. Strategies to reduce the impacts of roads on wildlife often focus on identifying and mitigating road mortality and barrier effects . However, the ‘road-effect zone’ may be just as detrimental to the ability of a species to persist in a landscape as other effects [3, 7–9], and requires consideration while planning and designing road projects .
The road-effect zone is the distance to which the ecological impacts of roads extend into the surrounding habitat [3, 7]. Road-effect zones have been quantified for birds [10, 11], mammals [e.g. 12–14], amphibians [e.g. 15–17] and reptiles [e.g. 18, 19]. The road-effect zone typically reflects a negative impact on wildlife , as within this zone, habitat is degraded and indirectly lost, evident through decreased activity or survivorship of individuals, and smaller populations [e.g. 3, 17, 20] compared to further away from the road. The size of the road-effect zone can be large: up to 1 km for some birds (e.g. Passeriformes and Piciformes) and up to 5 km for some mammals (e.g. Rodentia and Artidactyla) . Habitat degradation in the road-effect zone can be due to a number of factors, such as noise and light pollution, unsuitable vegetation type, and chemical pollution [3, 21]. Without accounting for the road-effect zone, the amount of habitat lost or degraded due to roads will be underestimated, which can potentially result in the loss of wildlife, ecosystem services and key ecosystem processes (e.g. predator-prey or plant-pollinator interactions) from the landscape . Understanding the size and the severity of the road-effect zone on a wide range of species will improve decision-making regarding strategies to avoid, minimize, mitigate and compensate the impact of roads on wildlife.
Many species of bats (order: Chiroptera) avoid the habitat adjacent to major roads and freeways [14, 23, 24]. This may be due to a lack of canopy cover [25, 26] or due to disturbances from the road and traffic, such as light and noise [e.g. 24, 27–29]. The size of the road-effect zone for bats can be highly variable—i.e. up to 500 m from a freeway for some species [23, 30], or up to 5,000 m for others [14, 31]. In highly cleared landscapes, such as agricultural areas, a large proportion of the habitat exists in verges adjacent to high-traffic freeways and roads. This means that the road-effect zone can potentially cover the entire extent of available habitat and drive bats out of the landscapes. Given their high trophic levels, widespread mobility and their responsiveness to anthropogenic stressors, bats are considered bioindicator species and in agricultural landscapes they also offer key ecosystem services such as pest-control and pollination [32–34]. Thus the loss of bats from such landscapes can be detrimental to ecosystem health, however the severity of the road-effect zone on bats in highly cleared agricultural landscapes is understudied and unclear [e.g. 30]. As a result, decision-makers may face uncertainty in how to best manage this landscape to reduce the negative impacts of roads on bats, and preserve bat presence.
The aim of this study is to quantify the road-effect zone for insectivorous bats (henceforth referred to as ‘bats’) in the agricultural landscapes of south-eastern Australia. Bats in this region can persist in highly cleared landscapes as long as there is some mature vegetation for them to roost in and forage around . However, a negative road-effect zone may hinder their ability to use mature trees in freeway verges. Using these results, we aim to suggest potential causes and mitigation options for the road-effect zone for bats in highly cleared agricultural landscapes.
Materials and methods
Research was conducted under Scientific Permit 10006093 granted by the Department of Environment, Land, Water & Planning.
This study was conducted in the predominantly agricultural landscape of central Victoria, Australia. This region is heavily cleared with remnants of heathy dry forest, grassy woodlands and box-ironbark forest , mostly existing in small patches, or linear strips such as roadside and freeway verges (Fig 1). The agricultural land is predominately used for grazing, with some opportunistic crop production . There are three major freeways in this region: Hume Freeway, Goulburn Valley Freeway and Calder Freeway. Within our study area, the freeways have two lanes of traffic in each direction and each carriageway is 12 m wide, separated by a vegetated median approximately 5–20 m in width. The maximum speed limit is 110 km/h. The annual average daily traffic volume (in one direction) averages 6,140 (range 5,800–6,300) vehicles/day along the Hume Freeway, 4,460 (range 3,700–4,800) vehicles/day along the Goulburn Valley Freeway and 6,720 (range 5,500–9,100) vehicles/day along the Calder Freeway . Vegetated verges along the edges of the freeways are on average 28 m in width (range 0–50 m) and typically consist of eucalypt woodland.
(A) Map of the study sites showing the three focal freeways in black, study transects in white. (B) Map of Victoria, Australia showing the three focal freeways in black. The grey box corresponds to the extent of A. (C) Example of a transect from an aerial view, showing the dual carriage freeway in black on the left of the frame and the transect in white. The yellow circles along the transect show detector placements at 10 m, 25 m, 50 m, 75 m, 100 m, 250 m, 500 m, 1000 m, 1,500 m and 2,000 m away from the freeway. (D) Side view of a wooden nest box with an Anabat detector within it, affixed to a tree approximately 1 m from the ground. The microphone was placed within a PVC pipe, oriented at 45° towards the sky. A and C were produced in QGIS (3.16.1-Hannover) using the base map layer, ESRI Satellite (ArcGIS/World_Imagery; Sources: Esri, DigitalGlobe, GeoEye, i-cubed, USDA FSA, USGS, AEX, Getmapping, Aerogrid, IGN, IGP, swisstopo, and the GIS User Community).
Each freeway is intersected by numerous linear strips of woodland vegetation which occur along, for example, property boundaries, waterways and farming roads (Fig 1). The vegetation in these linear strips can provide suitable habitat [35, 39–42] and commuting routes [42–45] for bats in this region. Small farming roads (i.e. single-lane, fewer than 100 vehicles per day) intersected the freeway perpendicularly and extended at least 2,000 m from the freeway, providing ideal “transects” for studying road-effect zone for bats. We surveyed bats along 18 transects distributed among the three freeways (Calder Freeway: n = 5, between -36.92150° S, 144.22181° E, to -37.09743° S, 144.35961° E; Goulburn Valley Freeway: n = 6, between -36.80396° S, 145.17779° E, and -36.94174° S, 145.14383° E; Hume Freeway: n = 7, between -36.57926° S, 145.91285° E and -36.84920° S, 145.34005° E; Fig 1). Transects along the same highway were between 1 and 19 km from the nearest transect (12 transects were within 5 km of the nearest neighbouring transect).
Recording and analysing bat call activity
We collected data in the austral summer between December 2014 and February 2015, when this region is predominately hot and dry with low to moderate humidity. Given the variability of the road-effect zone previously documented for bats, we chose to collect data in short intervals up to 500 m from the freeway as well as at larger intervals up to 2,000 m from the freeway (i.e. the length of the transects), to improve our chances of detecting a road-effect zone for bats. Data was collected at 10 distance intervals from the freeway along each transect: 0–10 m, 25 m, 50 m, 75 m, 100 m, 250 m, 500 m, 1000 m, 1,500 m and 2,000 m (Fig 1). The distance of the placement of the detector within the first interval (0–10 m) depended on where there was a suitable tree to install the detector on.
At each distance interval, we recorded bat calls using Anabat SD1 and SD2 model detectors, with unidirectional microphones that had been calibrated to have similar sensitivities (Titley Electronics, Ballina, New South Wales, Australia). To reduce the risk of theft, interference and damage, we disguised the detectors by placing them in wooden nest boxes. On the sides of the nest boxes, we attached a PVC pipe, oriented it 45° towards the sky and secured the microphone within the pipe opening (Fig 1). All nest boxes were affixed to trees (approximately 1 m from the ground), with the microphones pointing away from the freeway. We recorded calls at each transect for two consecutive nights, commencing half an hour before sunset and ending half an hour after sunrise, with all points along a transect surveyed concurrently. We surveyed two transects each night. Due to equipment malfunctions and absence of trees suitable for attaching the nest box, we were unable to collect a sample at each distance every night. In total, we collected 280 samples (out of a potential total of 360), with 21–36 samples at each distance out of a potential maximum of 36 (0–10 m: n = 29; 25m: n = 21; 50 m: n = 22; 75 m: n = 32; 100 m, n = 30; 250 m: n = 26; 500 m: n = 36; 1000 m: n = 28; 1,500 m: n = 32; 2,000 m: n = 24).
We identified the recorded Anabat zero crossing call sequences (henceforth referred to as “calls”) to species using the automated AnaScheme Bat Call Analysis System (Version 1.0) [46, 47]. A key was previously developed for this region using locally collected reference calls, which, when tested on an independent set of reference calls, was found to accurately identify 72% of the reference calls, with no mis-identifications while the remaining 28% were identified as ‘unknowns’ . We used this key to identify the calls we collected in this study. To further reduce misidentifications, we only attempted species identification when there were five or more valid pulses in the call and we deemed calls successfully identified when >50% of the pulses were assigned to the same species . We grouped calls from Nyctophilus geoffroyi, Nyctophilus gouldi and Myotis macropus, into a ‘Nyctophilus-Myotis complex’ because their calls are difficult to differentiate reliably from one another. We also visually confirmed any files identified as Austronomus australis as the key was prone to misattributing insect or background noise to this species. It was not possible to determine the number of individuals from the call data so our analysis and results reflect species activity rather than population sizes.
Environmental variables that may influence bat activity
Bat activity along transects could have been influenced by the amount and type of habitat available along the transect as well as the landscape surrounding the transect [30, 35, 48]. To minimize these effects, all transects were tree-lined on both sides of the road (transect verges were, on average, 8 m wide and ranged 1–30 m wide) and adjacent to agricultural fields and scattered residences.
The size of the trees and structure of the vegetation around each detector may influence the activity and presence of bats regardless of the distance from the freeway. Bats may prefer large trees (diameter greater than 30 cm at breast height) because they tend to have more hollows than smaller trees, which provides greater roosting opportunities , and have more flowers, greater peeling bark and greater canopy cover, which all support more insect prey . Therefore, we recorded the species and size (diameter at breast height) of all trees and visually assessed percentage canopy cover (to the nearest 10%) within a 10 m radius of each detector. A 10 m radius was adopted to avoid overlapping sampling areas because the first 5 detectors were 25 m from the adjacent detector.
Finally, to account for any influence that temperature and nightly variation in weather conditions can have on the presence and activity of bats [49–52], we obtained daily minimum temperature data (typically recorded overnight) from the Australian Government, Bureau of Meteorology (http://www.bom.gov.au/climate/data; weather stations were within 20 km of the sites).
To explore the change in activity of bats with distance from the freeway, we fitted Poisson regression models, using the number of calls per survey night (i.e. call rate, Ri) as the response variable. So, for each data point, i (each distance along the transect, per night): where λi was the mean call rate. Di was the distance from the freeway at which the detector was placed along the transect. More specifically, we used the log function Di = log(distance + 1) to reflect the diminishing strength with distance, as expected from a potential road-effect, and added 1 to the distance to avoid negative log numbers for distance zero. We compared this model using a linear relationship with distance (standardised) and found that the log approach provided better fitting models (either lower or similar DIC values).
To account for nightly variation in environmental conditions we included daily minimum temperature (Ti), and the number of large trees (Li) and canopy cover (Ci) within a 10 m radius of the detector. Finally, we included a random effect term for the transect, εx(i). Activity did not differ significantly among the freeways, so we combined the data from the three freeways. Daily minimum temperature and canopy cover were standardized around the mean. The intercept, β0, represents the baseline (0 m from the freeway, mean temperature, no large trees, mean canopy cover). All model fitting was conducted within a Bayesian framework of inference using Markov Chain Monte Carlo (MCMC) sampling, by calling JAGS 4.1.0  from R  using package R2jags . We ran three MCMC chains for each parameter, keeping 300,000 iterations after discarding a burn-in of 100,000, with a thinning of 10 to reduce the size of resulting files. We used vague uninformative priors for all parameters: uniform distributions U (-10,10) for all coefficients. Convergence was assessed by visual inspection of the chains and using the R-hat statistic (assuming no evidence of lack of convergence for values below 1.01). Models were fitted for the combined sum of the identified calls for all species combined and for each species separately. Since detectability differs among species, comparisons were made relative to each species’ activity along the transects, and not the absolute number of calls. Species richness did not differ among or within transects.
Defining the ‘road-effect zone’
We used the change in call activity (i.e. number of calls at each survey point) with proximity to the freeway as a measure of the road-effect zone. Some national management guidelines [e.g. in the UK, 56] use a 20% decrease in activity to signify a detrimental effect on bat populations. This is a conservative measure, which is used because effects such as the road-effect zone cannot necessarily be measured directly, for example in number of individuals killed at the road. Instead, road-effect zones can result in other, indirect, impacts, such as reduced fitness or foraging success, which are harder to measure in numbers. Thus, guidelines of relative loss are conservative measures used to acknowledge when there is a greater loss in activity than can be expected by natural fluctuations in bat activity . Therefore, in this study, we defined the size of the road-effect zone to be the distance from the freeway at which the activity of bats declines by 20% or more of their maximum activity along the transect monitored. Thus we: 1. determined the maximum activity per transect; 2. calculated 80% of that activity; and 3. determined the distance at which bats are 80% as active as their maximum, and therefore the distance over which activity had declined by 20% or more. We used this method to identify the size of the road-effect zone for all species combined, as well as for each individual species.
A total of 43,355 bat calls were assigned to 10 species or species complex (hereafter referred to as ‘species’ for simplicity), namely Austronomus australis, Chalinolobus gouldii, C. morio, Nyctophilus-Myotis complex, Ozimops ridei, O. planiceps, Scotorepens balstoni, Vespadelus darlingtoni, V. regulus and V. vulturnus. The mean number of identified calls per transect per night was 1204, and ranged from 47–2870 calls per transect per night. Results for each species are in S1 Table.
Evidence of road effect zone
We found that overall bat activity decreased with increasing proximity to the freeway, showing that the freeway had a negative effect on bat activity. The estimated regression coefficients for all species combined (i.e. total activity of all species) were (numbers in parentheses indicate the limits of the 95% credible interval): = 0.274 (0.260, 0.289) for distance from the freeway; = -0.176 (-0.198, -0.153) for daily minimum temperature; = -0.001 (-0.003, 0.001) for the number of large trees within a 10 m radius of the detector; and = 0.048 (0.037, 0.058) for canopy cover. Therefore, the activity of all species combined increased with distance from the freeway and canopy cover, decreased as the daily minimum temperature decreased and did not vary with changes in number of large trees, as there were large trees along all transects (i.e. the 95% credible interval for overlapped 0).
We identified a road effect zone (i.e. the proximity to the freeway at which call activity declines by 20% or more) for C. gouldii, C. morio, Nyctophilus-Myotis complex, S. balstoni, V. darlingtoni, V. regulus and V. vulturnus (Figs 2 and 3). The size of the road effect zone varied from 123 m (C. gouldii) to 890 m (V. regulus). There was no evidence of a road effect zone for A. australis and O. planiceps and conversely, O. ridei, showed a positive response to the road, with greater mean call activity closer to the freeway than further away (Figs 2 and 3).
Mean point estimates and 95% credible intervals for the regression coefficients included in the model for each species of bat separately, and in the model for all species combined (“Total Call Activity”) as the response. Data collected from central Victoria, Australia. Credible intervals overlapping zero indicate coefficients that had neither positive nor negative effects on the activity of bats (at α = 0.05).
Estimated mean call rate per night for each species of bat, with increasing distance from the freeway (when minimum daily temperature, number of large trees and canopy cover are held constant at their mean value). Error bars show the 95% credible interval of the estimated call rate per night. Shaded regions display the road-effect zone for each species (the distance from the freeway where activity of each species declines by at least 20%). Note the scale of the y-axes vary among plots, to assist in visualization. Data collected in central Victoria, Australia.
The negative road-effect zone for bats
A road-effect zone is evident when the habitat adjacent to a road supports less wildlife activity than the habitat further away. In this study, we demonstrate that bats are less active within several hundred meters of large freeways, compared to further away from freeways. Overall, the road-effect zone for the ten species we studied was 307 m wide, while the largest road-effect zone was 890 m wide for V. regulus, and the smallest road-effect zone found was 123 m wide for C. gouldii. Previous studies have demonstrated that bats in this highly cleared landscape can persist using small patches of remnant vegetation . In this region, freeway verges could match this description as many have the physical characteristics of good habitat for bats–large, mature trees providing both roosting and foraging resources. However, even the smallest road-effect zone is larger than the extent of the freeway-verge (on average 28 m wide in this study). Therefore, the freeway verges in this area may not support bats as much as would be estimated by the amount of physical habitat available, and the road-effect zone may effectively reduce the amount of suitable habitat for bats in this landscape.
Traffic is likely a large contributing factor to the road-effect zone for bats [57–59]. Bats can use roadside verges in cleared landscapes when the verges are adjacent to low-traffic roads (such as the transects in this study) and railway lines [30, 60, 61], however increased traffic volume reduces bat activity in the surrounding vegetation [30, 59]. Bats are at increased risk of collisions with vehicles where linear vegetation bisects freeways [24, 26]. Furthermore, traffic noise can restrict the ability of bats to hear prey and thus reduce their foraging efficiency [28, 29, 62]. However, as the area affected by traffic noise is likely to occur in close proximity to the freeway, it is unclear what could be causing the extended road-effect zone (i.e. up to 890 m) in our study. Other factors, such as lighting from roads/vehicles, and changes in vegetation structure are less likely to influence bats in the present study because the freeways were not lit and the vegetation structure did not change along the transects. It is also unlikely that prey availability influenced the change in bat activity, since the biomass of nocturnal, flying insects does not change with distance from the freeway in this study area . Therefore, the cause of the road-effect zone for bats is unclear. Future studies are needed to better understand why road-effect zones can extend hundreds of meters from a freeway, perhaps with a focus on the role road width and traffic volume play in the extent of the road-effect zone for bats.
The extent to which the freeway impacts different species of bat is highly dependent on their ecology. For example, the species that appear unaffected by the freeway, O ridei, O. planiceps and A. australis, tend to fly fast and high and can forage in open areas [35, 64]. As such, they may not be influenced by disturbances from the road, such as traffic noise [62, 65], like the other species which are slower, more manoeuvrable species that typically forage around trees . It may also be possible that the freeway-verge in our study area can provide resources such as availability of insects , in habitat where there is lower competition from other bats, creating an attractive foraging resource. This highlights the importance of considering the needs of all species when undertaking protection and mitigation works, as there are inter-specific differences.
Accounting for the road-effect zone in planning
Roads can have substantial and far-reaching impacts on the environment [4, 7–9, 20]. Quantifying the road-effect zone in management and road-planning processes is necessary to plan effectively for wildlife and their habitat requirements [66–69]. This information can help guide road-planning and decision-making on where to build roads, how to mitigate and reduce the impacts to wildlife and how much habitat is lost or degraded and needs to be compensated for. We suggest all future environmental impact assessments include quantifying the road-effect zone for sensitive wildlife, in order to best plan and mitigate the impact of roads on the environment. Furthermore, approaches to reduce the impact of the road-effect zone should be implemented. For example, creating verges with dense native vegetation may improve the quality of habitat adjacent to roads by reducing the amount of noise and light spill from traffic and lighting. The road-effect zone could also be compensated for by providing habitat further away from the freeway, which may include planting natural vegetation, or maintaining natural and unfragmented extents of available habitats. Finally, where possible, new roads should not be built in close proximity to habitat of sensitive wildlife. Incorporating road-effect zones into the environmental impact assessment for road projects will improve the chances of providing a landscape in which wildlife can persist despite human alteration of the landscape.
Identifying the extent of the road-effect zone can be difficult. For example, where species are rarely or never found near roads and only found far from roads, the presence of a road-effect zone is relatively clear. However, in situations like those presented in this study, where activity is reduced but not absent within the road-effect zone, it can be difficult to determine the biological significance of such reductions. In these situations, it is also important to consider species ecology, regular movement distances and habitual behaviours (such as a commonly used corridor etc.), as well as population viability, when identifying and mitigating the road-effect zone. Population studies could help determine if reduced activity is associated with a decline in abundance or vital rates that may affect a population’s capacity to persist within roadside environments or effectively incorporate roadside environments into their larger home ranges. As the thresholds likely vary based on type of road and the volume of traffic along those roads, a better understanding of the effect of road characteristics on the extent of the road-effect zone will help to design management strategies [2, 4, 8, 70].
Identifying a biologically relevant threshold can largely affect the recommendations and management strategies created for a given system. In this study, we used a 20% decline in activity to determine the size of the road-effect zone, based on best-practice guidelines in the UK . However, had we used different thresholds, we would have arrived at very different conclusions (Table 1). For example, if the threshold was to allow a 50% decline in activity, four species A. australis, C. gouldii, O. planiceps and O. ridei would have no road-effect zone, while, the most sensitive species, V. regulus would have a road-effect zone of 161 m, compared to the 890 m we identified using the 20% decline threshold (Table 1). Alternatively, if the threshold was to allow only a 10% decline in activity, only O. planiceps and O. ridei would have no road-effect zones, while the road-effect zone for V. regulus would be up to 1365 m from the freeway (Table 1). Additionally, the threshold value can influence management decisions, for example the calculation of habitat to offset. In current practises, offsets are usually created based on the magnitude of physical habitat lost. However, offsets should also reflect habitat that may no longer support species due to the road-effect zone, despite that habitat remaining physically available. The threshold used will determine the amount of habitat affected, as well as the extent of the effect. Therefore, it is important to choose a biologically relevant threshold as it can strongly influence the estimate of the road-effect zone, and the potential consequences to management.
Habitat indirectly lost or degraded within the road-effect zone can substantially change estimates of the amount of habitat available for wildlife to occupy. In this study, we quantified a negative road-effect zone, at least 123 m wide, for seven out of 10 species of insectivorous bats in southeast Australia. The road-effect zone for bats was overwhelmingly negative, and should therefore be considered in road-planning projects. Evaluating the road-effect zone early in environmental assessment processes can help guide decisions on road planning, building and mitigation strategies. Understanding the mechanisms and biological consequences of the road-effect zone can help develop appropriate and targeted strategies to reduce the impacts. Roads fragment much of our earth and understanding their full ecological impact is essential to maintain thriving wildlife populations and functioning ecosystems.
S1 Table. Summary of data collected.
Mean, median and range of number of bat calls per transect (combining 10 sampling points along each transect), per night for each species or species complex, across all three freeways (Hume Freeway, Calder Freeway and Goulburn Valley Freeway). Calls were collected at eighteen transects, over two consecutive nights at each transect.
VicRoads facilitated access to study sites. Thank you to the volunteers for helping to collect data, and to Cassandra Moore and Heather Hemmingmoore for providing feedback on earlier drafts of this manuscript. We also thank the two anonymous reviewers for providing feedback and helping to improve our manuscript.
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