Road barrier effect is among the foremost negative impacts of roads on wildlife. Knowledge of the factors responsible for the road barrier effect is crucial to understand and predict species’ responses to roads, and to improve mitigation measures in the context of management and conservation. We built a set of hypothesis aiming to infer the most probable cause of road barrier effect (traffic effect or road surface avoidance), while controlling for the potentially confounding effects road width, traffic volume and road age. The wood mouse Apodemus sylvaticus was used as a model species of small and forest-dwelling mammals, which are more likely to be affected by gaps in cover such as those resulting from road construction. We confront genetic patterns from opposite and same roadsides from samples of three highways and used computer simulations to infer migration rates between opposite roadsides. Genetic patterns from 302 samples (ca. 100 per highway) suggest that the highway barrier effect for wood mouse is due to road surface avoidance. However, from the simulations we estimated a migration rate of about 5% between opposite roadsides, indicating that some limited gene flow across highways does occur. To reduce highway impact on population genetic diversity and structure, possible mitigation measures could include retrofitting of culverts and underpasses to increase their attractiveness and facilitate their use by wood mice and other species, and setting aside roadside strips without vegetation removal to facilitate establishment and dispersal of small mammals.
Citation: Ascensão F, Mata C, Malo JE, Ruiz-Capillas P, Silva C, Silva AP, et al. (2016) Disentangle the Causes of the Road Barrier Effect in Small Mammals through Genetic Patterns. PLoS ONE 11(3): e0151500. https://doi.org/10.1371/journal.pone.0151500
Editor: Bi-Song Yue, Sichuan University, CHINA
Received: September 25, 2015; Accepted: February 29, 2016; Published: March 15, 2016
Copyright: © 2016 Ascensão 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: All relevant data are within the paper and its Supporting Information files.
Funding: The study was funded by Fundação para a Ciência e Tecnologia (FCT, MCTES, Portugal) through the project ‘Effects of habitat fragmentation on the population structure and connectivity of forest-dwelling species: a comparative landscape genetics approach’ (PTDC/BIA-BEC/101511/2008), a PhD grant (FA, SFRH/BD/38053/2007), and a Ciência 2007 contract (CF, C2007-UL-342-CBA1). Obrascón Huarte Lain, S.A. provided support in the form of salaries for PRC. This study also forms part of the CENIT-OASIS project funded by a consortium of companies supported by the Centro para el Desarrollo Tecnológico e Industrial, CDTI, of the Spanish Ministry of Science and Innovation. The Comunidad de Madrid, together with the European Social Fund, supports the TEG research group through the REMEDINAL-3 Research Network (S-2013/MAE-2719). The funders had no role in the study design, data collection and analysis, decision to publish, or preparation of the manuscript. The specific roles of all authors are articulated in the ‘author contributions’ section.
Competing interests: The authors have declared that no competing interests exist. Funding by commercial companies does not alter the authors' adherence to PLOS ONE policies on sharing data and materials.
Roads are ubiquitous features of contemporary landscapes worldwide and have a considerable impact on wildlife [1,2]. Roads can cause a barrier effect to animal movement and dispersal by representing a physical obstacle , when a large number of animal-vehicle collisions occur , or when animals display avoidance behavior towards the road or traffic [5,6]. In all cases, this barrier effect reduces the exchange of individuals between roadside populations, with demographic consequences  and possibly causing genetic subdivision [8,9]. This population subdivision, in turn, may accelerate the loss of genetic variation due to random drift and increased inbreeding, potentially leading to local extinctions [10–12].
Assessing the main drivers that influence road avoidance behavior is necessary to better understand and manage this barrier effect [5,13,14]. In particular, it is important to have a clear idea about the role of traffic volume in shaping road avoidance. If higher traffic volumes imply greater avoidance, these roads should be prioritized for mitigation. Research on movement data suggests that the presence of the road itself is the key driver for small mammal avoidance , whereas for larger mammals such as the wild boar Sus scrofa it is high traffic volume . However, an attempt to disentangle the relative importance of road surface and traffic volume to avoidance behavior has yet to be accomplished. Here, we develop a framework using genetic data to infer the main driver underpinning road avoidance behavior.
Comparison of genetic patterns has been used to assess population subdivision due to roads [8,9]. Our study is novel in that we implement a sampling design covering similar roads but with different traffic volumes and ages. We hypothesized that if populations on opposite roadsides were genetically differentiated, then lower divergence for roads with lower traffic volumes would indicate that traffic-related factors are the main component of the road barrier effect. However, depending on the temporal lag of the genetic effects, roads with higher traffic volumes but of different ages may exhibit comparable (Fig 1Ai) or distinct (Fig 1Aii) levels of differentiation. Conversely, if road surface avoidance is the main driver of genetic differentiation, two other scenarios are possible: 1) if genetic responses to road presence are fast, all roads should have similar genetic patterns (Fig 1Bi); or 2) if the genetic effects caused by roads have longer lag times, the roadside populations of older roads should have distinctive (higher) differentiation (Fig 1Bii).
Each square represents a road pictured according to its age and traffic. Darker/lighter color indicates higher/lower genetic differentiation, respectively. (A) Genetic patterns as a response to traffic volume (either due to road mortality or traffic avoidance). (B) Genetic patterns driven by road surface avoidance. In both cases, genetic effects caused by the roads may have short (i) or long (ii) lag times.
We focused our hypothesis testing on a small mammal, as this group can be particularly affected by the road barrier effect. For example, several studies using capture-mark-recapture and translocation techniques [5,6,16,17] and movement tracking [18–20] have suggested low crossing rates and/or inhibition of crossing movements. However, to date, few studies have examined the genetic patterns associated with the road barrier effect in small mammals [21–23], and none have evaluated the potential contribution of road avoidance. We were further interested in studying forest-dwelling species as these are more likely to be affected by gaps in cover such as those resulting from road construction. Accordingly, we chose the wood mouse Apodemus sylvaticus, a vagile species but for which there is evidence of low road crossing rates , as a model for our research. In the Iberian Peninsula the species is common and widespread , being especially abundant in evergreen woodlands and shrublands, where it is ecologically important as a common prey item for many predators , as a seed consumer , and as an acorn disperser .
We used microsatellite data to compare genetic patterns among wood mouse populations on the same and opposite sides of three highways of similar width but different traffic volumes and age. To quantify the strength of the genetic patterns, we examined if individuals from opposite highway verges were more genetically distinct than those sampled at a distance several times greater on the same side of the highway. We also estimated probable migration rates between opposite roadside populations. Studies such as this provide valuable insight for the development of appropriate measures to mitigate the road barrier effect, including prioritizing and defining the best locations and designs for wildlife passages, since their effectiveness depends on whether the animals avoid the roads themselves or the traffic they carry.
Materials and Methods
Study sites and design
The sampling sites were located along three highways on the Iberian Peninsula, one in Portugal and two in Spain (Fig 2). The width of the right-of-way of the highways was similar (ca. 60 m), including a central median strip (ca. 4 m) and grassy verges (ca. 10 m along each roadside). One highway (AP6) was considerably older and had a high traffic volume, while the other two were of similar age but with differing traffic volumes (Fig 2). Using this sampling design we could control for the three main confounding effects: (i) road width, since larger or extra traffic lanes may influence road crossing [16,28], and it has been shown to inhibit crossing movements of small mammals [16,17]; (ii) traffic volume, as it may reduce the probability of successful road crossing [28,29] and elicit different responses depending on the species ; and (iii) road age, as there is a time lag between landscape change and its effect on spatial genetic patterns .
Land cover was classified based on aerial photographs from Google Maps (accessed on December 1, 2015). Dense/sparse montado (oak woodlands) distinguishes between ‘high’ (>30%) and ‘low’ (<30%) tree cover (authors’ observation). Traffic volume is the number of vehicles passing between 2000 and 0600 h, as the wood mouse is a crepuscular species.
We sampled fenced highway verges, which are known to host high densities of wood mice [32,33]. The latter study, for example, estimated an average density over a two-year period near the highway of 5.58 ± 0.75 individuals/ha, against 1.74 ± 0.49 individuals/ha at 500 m from the highway and 3.96 ± 0.99 individuals/ha at 1000 m from the highway. The sampling sites were located in areas where the highways bisected oak woodlands (‘montado’), without any obvious signs of other human disturbance (e.g. urban proximity). The ‘montado’ is a traditional Mediterranean agro-silvo-pastoral system , mainly located in the southern regions of Portugal and Spain (where it is called ‘dehesa’). It is characterized by a scattered tree cover of varying density dominated by cork oak (Quercus suber) and holm oak (Q. ilex), with an understory composed of a mosaic of crops, grasslands, shrublands, fallow lands, and by extensive farming and livestock . Shrublands are dominated by species of Cistus, Erica, Lavandula, and Ulex. The sampling sites were chosen to be in areas where the highways pass through dense montado (>30% tree cover; authors’ observation), since wood mice may be less abundant in more open woodland [36,37].
For each highway, we analyzed two sampling sites to assess the consistency of genetic patterns, with each site comprising two trap lines (one in each side of the highway). Distance between sites was ca. 3500 m for AP6, 1500 m for A2 and 1200 m for AP51, and the minimum distance between the Spanish highways (AP6 and AP51) was 13 km. Distances between sampling sites were greater than four home range diameters (ca. 1000 m; assuming a circular shape) of the largest territories reported for wood mice, ca. 5.04 ha . Considering that a mean home range area of 1.12 ha has been estimated in oak woodland in the Iberian Peninsula , we assumed that the probability of individuals moving between sampling sites was negligible.
Highways in the Iberian Peninsula have numerous regularly spaced culverts (about one per km) for water drainage. Close to the sampling sites, there was a culvert in the first site of A2 and AP6. The first A2 site also had an overpass nearby, while both the first AP6 site and the first AP51 site had a nearby underpass. There was a viaduct in between the A2 sites (ca. 500 m in length and about 100 m from the first site) and in between the AP6 sites (ca. 200 m in length and about 150 m from the second site), and an overpass between the AP51 sites at about 130 m from the first site.
Sampling was conducted between February and May of 2010. At each study site, sampling was carried out until about 25 adult wood mice were sampled from each side of the highway, which was generally achieved in less than 15 consecutive sampling days. Each trap line had 60–100 baited Sherman™ live traps, placed 10–20 m apart, mostly in the highway verges and where higher capture rates were expected (near oak trees or shrubs), along ca. 400 m of the highway and up to 50 m from the pavement. Where required, oral permission to access private land to conduct the study was obtained from the owners. Permission to access highway verges was obtained from highway companies. Bread fried in rancid oil was used as bait and cotton-nesting material was provided inside each trap as bedding to protect captives from low temperatures. In addition, traps were hidden under vegetation cover to protect animals from adverse weather conditions and to avoid detection by predators. Traps were reviewed at dawn to minimize the time that animals were kept inside.
Each individual captured was weighted, sexed and marked with a fur-clipping code denoting trap line identification, and released at capture location. Individual marking aimed to detect road crossings and to avoid resampling individuals. Individuals of less than 15.5 g were classified as juveniles and those above this weight as adults [39,40]. For each adult we collected approximately 1 cm of the tip of the tail or an ear biopsy, which were preserved in a salt-saturated 20% dimethyl sulphoxide (DMSO) solution  for DNA extraction. The cuts were disinfected with antiseptic solution. We did not carry out a specific post-release monitoring of the animals, but we noticed that some first captures already lacked the tip of the tail, possibly due to intra- and interspecific fights or predation attempts. Moreover, 11% of the individuals were recaptured at least once on subsequent days of sampling (see Results) and all seemed to be in good condition. These observations suggest that clipping a small section from the end of the tail should not affect a wood mouse’s survival.
Capture and handling of animals were in conformity with Portuguese and Spanish nature conservation directives (Instituto da Conservação da Natureza e das Florestas in Portugal; Dirección General de Medio Natural in Spain) and in compliance with the European Communities Council Directive 86/609/EEC for animal experiments, and were carried out under the permit of Dirección General del Medio Ambiente de la Junta de Castilla y León (CML/mjg; File: EP/CYL/424/2009) and of Instituto da Conservação da Natureza e das Florestas (254/2009/CAPT). The ethics committee for Animal Care and Use from the Faculdade de Ciências da Universidade de Lisboa—Organismo Responsável pelo Bem-Estar dos Animais, ORBEA—approved all procedures for capture and handling (form 1/2015 ORBEA).
Genomic DNA was extracted from all samples using the EZNA Tissue DNA Kit (Omega BioTek) following the standard protocol for animal tissue. We obtained complete multilocus genotypes by PCR amplification of nine microsatellite loci isolated from Apodemus sylvaticus, A. agrarius, A. flavicollis and A. draco: As7, As11, As20 and As34 , TNF(CA) , SFM2 , and SCFM2, SCFM6 and SCFM9  (S1 File). PCR products were run with a GS-500 ROX size standard on an ABI 310 Genetic Analyzer (Applied Biosystems), and scored using Genemapper version 3.7 (Applied Biosystems). Alleles were assigned using bins created in TANDEM version 1.08 . Genotyping was validated by re-amplification and re-analysis of 15% of the samples.
Microsatellite genetic variation.
For each sampling line, we checked the microsatellite loci for deviations from Hardy–Weinberg equilibrium (HWE) and linkage equilibrium using, respectively, a probability test and a likelihood ratio test in the program GENEPOP 4.2 . We used α = 0.05 and p-values were adjusted by sequential Bonferroni correction for multiple tests . We used MICRO-CHECKER 2.2.3  to check for allelic dropouts and mis-scoring due to stuttering, and ML-NullFreq to estimate the frequency of putative null alleles using a maximum likelihood method . We calculated number of alleles, observed and expected heterozygosity, and inbreeding coefficients using GENETIX 4.05 . We used GENALEX 6.5 [52,53] to determine the number of private alleles for each sampling line relative to the one on the opposite roadside, with a minimum allele frequency of 0.05 to account for sampling and genotyping errors. Because relatedness may bias estimates of genetic differentiation among populations, we calculated the average pairwise relatedness for each sampling line using the Queller and Goodnight mean estimator  in GENALEX. The 95% confidence intervals around the mean values were estimated using 10,000 bootstraps.
We evaluated the statistical power of the microsatellite data set to detect population differentiation using POWSIM 4.1 . This program simulates genetic sampling from populations that have drifted apart to a particular expected value of FST, specified by the user, and the population samples are used for testing the null hypothesis of genetic homogeneity. We tested three scenarios for an FST of 0.008 (the lowest observed value; see Results), with allele frequencies and sample sizes as for each of the sampling sites with the lowest FST between opposite roadsides. One thousand simulated data sets were generated for each scenario, and the proportion of significant outcomes (P<0.05), i.e. an estimate of power, was determined using Fisher’s method to combine exact P-values across loci.
Comparing genetic signatures of the road barrier effect.
To compare genetic differentiation patterns between highways we performed different analyses, as the lag time for detecting a new barrier can be highly dependent on the analytical techniques used [31,56,57]. These analyses focused on three classes of methods: exact tests of population differentiation, FST and related measures, and allele frequency-based genetic distance.
Genetic differentiation was tested in GENEPOP using a log-likelihood (G)-based test , without assuming random mating within samples. We used Fisher’s method and a generalized binomial test implemented in MultiTest 1.2  to evaluate overall significance across loci.
We estimated FST  and, because this estimator of genetic differentiation can be influenced by the amount of within-population variation, also G”ST  and DEST  using GenoDive 2.0b24 . Significance was tested using 20,000 permutations, and 95% confidence intervals (CIs) were obtained by bootstrapping across loci. We used FreeNA  to obtain genetic differentiation (FST) estimates with an ENA (excluding null alleles) correction. We also used the chord distance (Dc)  to measure genetic differentiation. Dc has been applied in landscape genetic studies [21,66], being robust to low null allele frequencies . Also, allele frequency-based genetic distances may be more sensitive than FST in detecting the effects of recent barriers to gene flow . Chord distances were calculated with FreeNA and 95% CIs were obtained by bootstrapping over loci (1000 replicates).
For the genetic differentiation estimates, we compared results across roadsides against those from same roadside using a differentiation index (dGD) [67,68]. We computed dGD as the mean differentiation between trap lines on opposite sides of the highway minus the mean differentiation between trap lines on the same side of the highway. Positive values of dGD indicate that individuals from opposite roadside trap lines are more genetically distinct than those from same-roadside trap lines. However, as sampling sites were not equidistant we could not control for distance effect and therefore a negative value was not informative. We then bootstrapped individuals 1000 times for significance levels. Under the null hypothesis of no differences between opposite and same-roadside trap lines, dGD should follow a normal distribution centered on zero. Conversely, under the alternative hypothesis (i.e. higher genetic differences among individuals from one of the groups), dGD should be significantly different from zero. We considered the difference to be significant when more than 95% of the test values were greater or less than zero. To test independence of the results from the chosen metric, dGD was performed using both Dc and FST.
Estimating migration rates between opposite roadsides.
To estimate migration rates between opposite roadsides, we carried out computer simulations parameterized for five variables (Table 1). Simulations consisted of two populations initially exchanging 50% of individuals in each generation (‘pre-highway’) and then we introduced a linear barrier (‘highway’) that bisected the landscape, after which the two populations (roadsides) exchanged 20%, 10%, 5%, 1% or 0% of individuals.
Simulated populations had 54 individuals (mean value across sampling lines of effective population size, Ne, estimates from LDNe , see Table A in S2 File), characterized for nine microsatellite loci, with maximal initial variability and a maximum of 30 possible allelic states (‘Initial alleles’ in Table 1). We assumed free recombination between loci, a stepwise mutation model , and a mutation rate of 0.0005 [73,74]. For simplicity, we assumed discrete generations, a single reproduction per lifetime, equal sex ratio, random mating and constant size in each population. We also considered that road mortality could be discounted given the evidence of low road crossing rates in wood mice (see Results and [6,39,40]). Since it is unlikely that roadside populations are completely isolated from adjacent (unsampled) populations on the same side of the highway [23,75], a number of same-roadside immigrants replaced a same number of randomly selected residents in each generation (see Table 1 for details).
Simulations were run for 1000 generations and the barrier was introduced at generation 500. One thousand replicates were computed for each of the five tested between-roadside migration rate values. Simulations were performed in a model written in NetLogo 5.3  that mimics EASYPOP  capabilities and options, but allows more flexibility in parameter settings and output (code available in S3 File). For each migration rate scenario, we calculated the values of FST, G”ST, DEST and observed heterozygosity (Ho) in each generation, based on samples of 25 individuals from each population. From these datasets we plotted the 5–95% envelope and superimposed the observed values for comparison.
While the population sizes were set based on the estimates of Ne for the roadside sites, for the other parameters we did not have empirical results and thus the chosen values were taken from the literature (mutation rate) or subjective guesses (e.g. same roadside immigrants). Therefore, in order to understand how the model parameters could have affected our results, we performed a sensitivity analysis to explore multiple model parameterizations (within a range of alternatives to the default parameter values, Table 1). In the sensitivity analyses the parameter under test had a random value within the respective variation range, while the other parameters were set to default values. We ran 500 simulations for each combination of parameter and migration rate (25 combinations in total).
We captured 386 wood mice, 6% of which were classified as juveniles. Forty-four individuals were recaptured at least once (total number of recaptures = 226), but there were no recaptures on opposite sides of the highways, i.e. no road crossings were detected.
Microsatellite genetic variation
We genotyped 302 adults (n = 101 in AP6, n = 101 in A2, n = 100 in AP51), corresponding to a minimum of 23 samples per sampling line. There was no missing data (S1 File). The error rates per allele and per genotype [78,79,80] were 0.016 and 0.032, respectively. Forty-three percent of the genotyping error was associated with locus As11. Deviations from HWE were observed in zero to three loci across sampling lines, being more frequent at locus As11 (Table B in S2 File). Results from MICRO-CHECKER and ML-NullFreq indicated a higher frequency of null alleles at the same locus, but the estimated null allele frequencies for As11 were greater than 0.1 only in four of the 12 sampling lines, and never exceeded 0.2 (Table C in S2 File). Moderate null allele frequencies (< 0.2) should have a limited effect on measures of genetic diversity and differentiation over all loci [81,82]. The fact that corrected FST values using FreeNA were nearly identical to the uncorrected values (see below) also suggested that the possible presence of null alleles did not introduce a significant bias in our analyses. Significant linkage disequilibrium was found only between loci As20 and As34 at two sampling lines of highway A2 and between As20 and SCFM9 at two sampling lines of highway AP6. Therefore, we decided not to exclude any loci from further analyses. Overall, our data indicated similar levels of genetic variation, inbreeding and relatedness among the 12 sampling lines, with the mean number of alleles per locus ranging from 13.3 to 17.0, the mean observed heterozygosity from 0.76 to 0.85, the inbreeding coefficient from 0.09 to 0.17, and the mean pairwise relatedness from 0.02 to 0.06 (Table D in S2 File). These results suggest that inbreeding and relatedness within sampling lines did not contribute substantially to the observed patterns of genetic differentiation. Measures of microsatellite diversity were comparable to those found in other population samples of wood mice [42,83,84]. The number of private alleles varied between trap lines, but differences were not statistically significant (χ2 test = 12.6, df = 11, p > 0.32). Based on the POWSIM analyses, the statistical power of our microsatellite panel for detecting genetic differentiation was high, with a probability of 85% or more of detecting FST ≥ 0.008.
Comparing genetic signatures of the road barrier effect
The G-tests indicated genetic differentiation (p<0.05 in all cases) both between opposite roadsides and same-roadside sampling lines for all three highways. This was corroborated by the significant values of FST and related metrics (p<0.05) and the estimates of genetic distance Dc (Figs 3 and 4; Tables E and F in S2 File). Values of G”ST and DEST were considerably higher than FST (Tables E and F in S2 File), which is expected when within-population heterozygosity is high . Overall, we detected significant differentiation between opposite roadsides and among same-roadside trap lines in all highways. The fact that there was a large overlap in the levels of genetic differentiation across comparisons supports the hypothesis that road surface avoidance is the main driver shaping the barrier effect for wood mice, and that significant genetic differentiation can develop within short periods after a highway has been built (Fig 1Bi). Conversely, there was no evidence to support the hypothesis of genetic differentiation being mainly due to a traffic volume effect, as we did not find lower differentiation for AP51 (Fig 1Ai) or a gradient of differentiation from AP51 to AP6 (Fig 1Aii).
Green and orange lines represent the genetic differentiation observed between, respectively, sampling lines on opposite roadsides and on the same roadside. Dots represent mean values and limits are 95% confidence intervals.
Green and orange lines represent the genetic differentiation observed between, respectively, sampling lines on opposite roadsides and on the same roadside. Dots represent mean values and limits are 95% confidence intervals.
The resampling-based test for differences in genetic distance Dc between opposite and same-roadside sampling lines provided evidence for higher average across-road differentiation for highways AP6 and AP51 (Fig 5). For highway A2, however, the genetic distance between same-roadside sampling lines was on average greater than between opposite sampling lines. Results using FST were similar (not shown).
Positive values indicate higher average differentiation of samples between opposite roadsides relative to same-roadside samples. For AP6 and AP51, over 97% of the resamplings yielded test values greater than zero. For A2, all resamplings gave values less than zero.
Estimating migration rates between opposite roadsides
The sensitivity analysis of the simulation model over the tested parameter ranges suggested that ‘Population size’ and ‘Same-roadside immigrants’ were the parameters that most significantly influenced FST, G”ST, and DEST (Fig A in S2 File). However, the parameter ‘Same-roadside immigrants’ only had a large effect under the scenario of complete isolation between roadsides, and in the case of FST also when the migration rate was 0.01. G”ST and DEST, but not FST, were also sensitive to the initial number of alleles, particularly when the across-road migration rate was ≤ 0.01. A higher sensitivity of DEST to the initial level of genetic diversity as compared to FST has been observed previously .
After ‘highway’ introduction, the increase in FST, G”ST and DEST values was inversely proportional to the level of gene flow (Fig 6). The three estimators reached a new ‘equilibrium’ value relatively rapidly at between ten and 40 generations after ‘highway’ establishment. This result is in agreement with previous studies showing that at high mutation rates the time taken to reach 95% of the equilibrium value is similar for the three statistics [61,86], and that equilibrium can be reached faster when heterozygosity is high and Ne is not very large [85,87]. However, when the assumed migration rate was very low, FST took a longer time to reach ‘equilibrium’; this behavior of FST has been reported before . Moreover, values of G”ST and DEST increased much faster than FST, as in the simulations of  and , thereby facilitating earlier detection of the barrier. Observed values of FST, G”ST and DEST were consistent with those estimated from simulations with a migration rate of 5–10% (Fig 6). In particular, the observed values of the latter two parameters closely matched the simulation results for a migration rate of 5%. As shown by the results of simulations assuming an Ne of 20 or 100 for each roadside site (Fig B in S2 File), so as to cover the range of the mean Ne estimates from LDNe for the 12 roadside sites (Table A in S2 File), the actual inferred migration rate depends on the assumed Ne. The main point is that, for a plausible range of Ne values, the patterns of across-road genetic differentiation for the three highways are compatible with recurrent migration rates that are relatively low and, despite differences in age and traffic volume, similar among highways.
For each migration rate (m), the plots in the left panel show the evolution of the parameters through the simulation and the plots in the right panel show a detail of the simulations for the period in which the ‘highway’ has been introduced (apricot areas in the left plots). The 5–95 percentile envelopes (999 replicates for each migration rate value) are shown in light coral. In the right plots, the blue circles represent observed values, which are placed to the right of generation 500 according to the highway’s age and assuming a generation time of six months .
In this study we used different population genetic methods to investigate the presence and causes of the road barrier effect. We performed a comparative study of three highways of similar width but differing in age and traffic volumes, and used the wood mouse as a model species of forest-dwelling small mammals. The results of the different analyses provide consistent evidence for the presence of a highway barrier effect in the wood mouse apparently due to road surface avoidance. This conclusion is supported by the generally similar genetic patterns observed across the three studied highways. If road mortality or traffic avoidance were major components of the barrier effect, genetic differentiation between opposite roadsides should have been lowest for the highway with the lower traffic volume, but this was not evident in any of our analyses. Besides, if road age was a primary factor, we would expect genetic differentiation between opposite sides of the older highway to be significantly higher, but this was also not supported by our data (Figs 3 and 4). The hypothesis that best fits our results is that road surface avoidance is the primary cause of the barrier effect and that genetic responses to highways among wood mouse populations in our study area have short lag times (Fig 1Bi). Other road genetic studies have demonstrated that genetic divergence can develop rather quickly when the barrier to gene flow is strong [9,21,68,89]. In each sampling site, the distance between trap lines was about 150 m and the maximum distance between traps was ca. 500 m. Since studies on wood mice have recorded dispersal movements of at least 300–500 m [90,91,92,93] and frequent excursions of 100–250 m beyond home range boundaries [90,94,95], the genetic differentiation observed between opposite trap lines is interpreted as due to the highway and not to isolation by distance . In this context, we note a recent study reporting non-significant pairwise FST values of 0.008–0.014 between arable sample sites 1.5–6 Km apart in a farmland landscape intersected by roads and rivers . Thus, even wood mice separated by much greater distances than those between opposite trap lines in our study are not necessarily significantly genetically differentiated. In addition, there is no evidence of previous barriers such as rivers or streams at the locations of the studied highway segments that could have caused the observed genetic differentiation. It is possible that the importance of traffic and road age is greater on older highways or those with higher traffic volumes than those studied here, and this hypothesis requires further investigation.
For AP6 and AP51, wood mice on opposite roadsides, despite being only about 150 m apart, were on average more genetically distinct than wood mice from sampling lines on the same side of the highway but more than 1 km apart and separated by viaducts (Figs 3 and 4). This result is revealing since one might have expected genetic differentiation to be greater among same-roadside samples given the distance between them and the results of previous studies of genetic structure in wood mice [83,84]. The lower across-road differentiation found in the A2 may be due to the higher number of culverts on the studied segment of this highway than on the segments of the other two highways (author’s observation). Wood mice are known to use highway crossing structures, including culverts , underpasses  and overpasses , and this may reduce the barrier effect. In agreement, on all three highways the genetic differentiation between opposite roadsides was lower at the sampling site with crossing structures nearby (Figs 3 and 4). Wood mice tend to avoid open terrain without ground cover that could offer protection from predators [24,101], and this has been invoked to explain fine-scale genetic structure  and inhibition of road crossings . Our results indicate that highway passages may provide landscape connectivity for wood mice and reduce genetic differentiation between roadside populations.
The low FST values (0.008–0.028) could be interpreted as suggesting high migration rates between opposite sides of highways, but genetic differentiation measured by FST is constrained when within-population heterozygosity is high [102,103,104], which is the case for all our highway sites.  showed that the lag time for detection of a new barrier could be long using FST, but much shorter using standardized GST. Actually, the magnitude of standardized GST values we found between opposite roadsides is comparable to that obtained between populations 0.85–3 Km apart in a study of microgeographic structure in wood mice .
Similarly to our case, previous road genetic studies in small mammals have found non-significant or low FST values between highway sides: 0.018–0.048 ; 0.0018 ; and 0.005–0.036 but non-significant . This may be due to the aforementioned deflation of FST with high subpopulation heterozygosity  or the lag time associated with FST. This lag time should increase with larger Ne, and this reasoning has been used to explain the lack of genetic differentiation between common vole Microtus arvalis populations separated by a 25-year-old motorway . In contrast,  asserted that the genetic differentiation they observed between bank vole Myodes glareolus populations separated by a highway of the same age could be expected because such time period corresponds to 25–50 generations of bank voles. In the common vole study, support for the inference of a very large Ne may be due to the assumption that the motorway led to two completely isolated populations, which might be an extreme scenario given the evidence of road crossing attempts by the species [105,106]. More generally, different results between studies on the effect of roads on genetic differentiation may be partly due to differences in study design and scale [9,68], with some studies sampling over relatively large areas of the landscape [22,107] and others sampling from both sides of individual roads [21,68].
Our LDNe estimates of Ne for the roadside sites ranged between 20 and 100 (Table A in S2 File); previous studies of genetic structure in wood mice also inferred small local Ne [84,97]. The linkage disequilibrium (LD) method implemented in LDNe can provide precise Ne estimates for relatively small populations (Ne < 200), is not likely to mistake a population with moderately small Ne for one with large Ne (and vice-versa), is robust to equilibrium immigration rates up to 0.1, and performs well in populations with skewed sex ratio or non-random variance in reproductive success [108,109,110]. However, the underlying model for the LD method assumes discrete generations; when samples are taken from age-structured species, the estimate from the LD method can be an estimate of the effective number of breeders (Nb) that produced the cohort(s) from which the sample was taken or of a quantity intermediate between Nb and Ne [108,111]. Recent work suggests that estimates from the LD method based on random samples of adults may be on average 20–30% lower than the true Ne per generation, but the downward bias tends to be less in species in which the reproductive lifespan approaches the generation length  (see below). In our simulation, we assumed a constant (moderately small) Ne within the range of the LDNe estimates across sampling lines. The rationale for this choice was that, given our estimates of contemporary Ne and the large annual population fluctuations of wood mice [33,113], the multigeneration Ne may be expected to be moderate [114,115]. If this Ne is larger than we assumed, as possibly indicated by the values of FST (<0.05) and DEST (>0.1) between opposite sides of the highways (Table E in S2 File) , then the migration rate may be lower than that inferred from the simulation [e.g. 89]. A strong road barrier effect combined with a moderate multigeneration Ne may explain why we were able to detect significant across-road genetic differentiation after 20 generations of wood mice. It could be argued that the fact that we detected differentiation even for the newest highways (ca. 10-years-old) could be due to the relatively small roadside samples used in this study [116,117], but the inference of a road barrier effect is supported by the greater average differentiation observed between individuals from opposite roadsides than between those more than 1 Km apart on the same roadside (Fig 5). Moreover, another study on wood mice, with sample sizes per site and number of microsatellite markers used similar to those in ours, found greater average differentiation between urban than arable sites, with the latter for the most part not significantly differentiated from each other . However, future research, sampling more individuals along more extensive stretches of the highway verges, is needed to confirm our results.
In agreement with previous genetic studies pertaining to roads, which generally found reduced but ongoing gene flow between opposite roadside populations (reviewed in , our simulations indicated limited connectivity across the highways. Combining empirical and simulation analyses can be a powerful approach in landscape genetic studies [118,119]. Here, we used a simple simulation model that yielded FST, G”ST and DEST values compatible with observed ones when the assumed across-road migration rate in the simulations was about 0.05. These results further support the conclusion that gene flow is restricted between roadsides and of the same level across the studied highways, despite differences in age and traffic volume, so that they exhibit similar genetic patterns. The inferred gene flow may be the result of the numerous regularly spaced culverts in the studied highways, but given the relatively low migration rate estimated, which could be even lower if the local Ne of the roadside populations are larger than we assumed (Fig B in S2 File), such passages are perhaps not effectively counteracting the road barrier effect. Nevertheless, we highlight that the surveyed sites without passages had higher, albeit not significantly different, genetic differentiation. This suggests that crossing structures may indeed improve the permeability of highways to wood mice movement. However, a significant interchange of individuals per generation may be needed to prevent substantial population differentiation [120,121], for example when the ratio of effective population size to census population size (Ne/N) is small [122, 123] or when migrants are likely to be at disadvantage in terms of survival and breeding success, as in the case of territorial species .
The most subjective parameter in the simulations was related to the number of immigrants received in each generation from neighboring populations on the same side of the highway. This parameter was included in the model because it is unlikely that roadside populations are isolated from other populations on the same side of the highway and, since observed individuals were highly polymorphic, to prevent fixation of alleles during simulations. We assumed that, for each roadside and in each generation, a single immigrant replaced a resident. The sensitivity analysis showed that variation in this parameter would significantly affect model predictions for Ho. However, increasing the number of immigrants raised the values of Ho (Fig A in S2 File) so that their averages were more dissimilar from those of the observed data (Table D in S2 File). This further suggests that the model assuming one same-roadside immigrant into each roadside population could accurately infer the most probable maximum migration rate between opposite roadsides. Our simulations contained a number of simplifying assumptions regarding life history and demographic traits, including sex ratio, mating process, breeding frequency, and population size. We are not aware of specific estimates of generation time for wood mice. The maximum longevity in the wild is 15–20 months [124,125], and some studies found few individuals living for more than 12 months [126,127,128]. Generation time is often approximated by considering maximum longevity in the wild and age at first breeding, since the latter sets the generation time . The age at first birth in the wood mouse is three months  and generation times of similar length have been estimated for other small rodents . However, there is individual, seasonal, habitat-related and geographical variation in the age of sexual maturity [125,132,133,134], and the onset of sexual activity in females as a function of age can be delayed and slow [24,135]. Taking all this information together, we assumed a generation time of six months . We also assumed an equal sex ratio. A slightly male-biased sex ratio (≈ 55:45, ) has been reported by several authors [133,136,137,138], while others have found a surplus of females among reproductive individuals [135,139]. In general, it is known that the sex ratio fluctuates yearly and seasonally, but it tends to become balanced before the start of the breeding season [125,136,137]. We assumed one reproductive event per individual because, although females can produce up to four litters annually , most (≈ 90%) breed only once or twice in their lifetime . Wood mouse population dynamics is also complex with, for instance, seasonal and annual population fluctuations due to density-dependent factors and food availability [113,137,138,140]. Although we believe that our simulation could capture the main population dynamics and replicate the genetic patterns among wood mouse populations separated by barriers of varying permeability, future work should aim to develop more complex models that more realistically incorporate the biology and ecology of the species, including the occurrence of road mortality [99,141,142].
The importance of comparing genetic and ecological data in understanding population structure and connectivity has been repeatedly highlighted [21,118,143]. Our results, concerning both the inferred reduced gene flow and the lack of observed road crossings in the recapture data, concur with the findings of road ecology studies on wood mice . For example,  recorded only four road crossings in a total of 994 recaptures (576 individuals) and  found that only six among 98 marked individuals (559 recaptures) crossed minor rural roads. Unpublished capture-mark-recapture data gathered by one of us (FA; sampling design described in ) also indicate that wood mice rarely crossed highway A2, with only five crossings between verges and the median strip in 251 recaptures of 124 individuals. However, direct measures can overestimate gene flow since dispersing individuals may not breed , or underestimate migration as they only record the sampling period and may miss seasonal or other movements . Thus, comprehensive genetic analyses are invaluable in providing reliable estimates of gene flow and population differentiation (e.g. [68,89,107]).
This study provides evidence for the presence of a highway barrier effect in the wood mouse apparently due to road avoidance. This is likely an expression of behavioral avoidance of open areas [5,6,16,101] and not as a result of an inhibition to cross paved roads, as both attempted and successful paved road crossings have been recorded [39,40,99,141]. A road barrier effect due to road clearance avoidance is likely to occur in other small forest mammals [6,16,17,145]. The wood mouse is abundant, widely distributed, and not considered of conservation concern, but it is still important to maintain genetic cohesion among populations, particularly given the high density of the road network across its range. Thus, management measures that have been proposed to increase across-highway connectivity for small mammals, and also for other wildlife [146,147], would be worth considering. Although the effectiveness of crossing structures for maintaining genetic connectivity needs to be evaluated and monitored in the long term, they remain one of the few viable options for mitigating the effects of highways on small to medium-sized species [5,148,149]. One form of mitigation could be retrofitting of culverts and underpasses to increase their attractiveness and facilitate their use as highway crossings for wood mice and many other species. The use of culverts by wood mice and other small mammals has been reported in previous research [98,146,147], and our work also suggests a positive effect of these structures. Also, roadkill studies have found lower mortality of wood mice in road sections with culverts and underpasses [99,150]. Small mammals may prefer small culverts than underpasses with larger diameters and may preferentially use passages with abundant vegetation cover at entrances [17, 148,151]. Moreover, the retrofitting of road passages should ideally be undertaken in areas where verges have a mature vegetation structure, as they are known to provide refuge habitats and corridors for small mammals [32,33,152]. Accordingly, we suggest that mowing of verges, which is used to prevent vegetation from encroaching on the roadway and for traffic safety reasons, could be limited to a certain distance (ca. 10–12 m) from the pavement edge, with the rest of the verge managed to promote growth of tall and dense vegetation [16,17,32,33]. These roadside vegetation strips would facilitate establishment and dispersal of small mammals.
In conclusion, here we used the wood mouse as a model in a study designed to disentangle the causes of the road barrier effect and investigate the role of road avoidance through the analysis of genetic patterns, and the results contribute to our understanding of how small mammal populations may be affected by highways . Moreover, it adds to the growing literature demonstrating that roads can have a rapid effect on the genetic connectivity and substructuring of wildlife populations.
S1 File. Microsatellite genotypes.
Microsatellite genotypes of the 302 wood mice samples arranged by trap line in GENALEX format.
S2 File. Tables A-F, Figs A-B.
Estimates of effective population size using LDNe and ONeSAMP (Table A). Original and adjusted p-values for the HWE test (Table B). Loci with possible null alleles identified by MICRO-CHECKER (Table C). Estimates of genetic diversity for each trap line (Table D). Estimates of genetic differentiation between opposite highway sides for each of the three studied highways (Table E). Estimates of genetic differentiation between same-roadside sampling lines for the three studied highways (Table F). Sensitivity analyses of FST, G”ST, DEST and Ho to variation in the model parameters: ‘Population size’, ‘Initial alleles’, ‘Mutation model’, ‘Mutation rate’ and ‘Same-roadside immigrants’ (Fig A). Values of FST, G”ST, DEST and Ho through time (generations) estimated from computer simulations for different migration rates after a ‘highway’ replaces at generation 500 a previous scenario of panmixia and assuming a multigeneration Ne of 20 or 100 for each roadside site (Fig B).
We thank D. Reto, L. Gaspar, F. Moreira, C. Marques, L. Kuc, A. Planillo, E. Iranzo and J. Hernández for helping with fieldwork and J. Mullins for laboratory work. We are grateful to two anonymous reviewers for comments that helped us improve the manuscript. We acknowledge Companhia das Lezírias, Instituto da Conservação da Natureza e das Florestas, and Brisa (Auto-Estradas de Portugal S.A.) for fieldwork permits and logistical support.
Conceived and designed the experiments: FA CM JEM CF. Performed the experiments: FA CM JEM PRC CS APS. Analyzed the data: FA CF. Wrote the paper: FA CF. Read and approved the final manuscript: FA CM JEM PRC CS APS MSR CF.
- 1. van der Ree R, Smith DJ, Grilo C. Handbook of Road Ecology. Chichester, UK: John Wiley & Sons, Ltd; 2015.
- 2. Forman RTT, Sperling D, Bissonette JA, Clevenger AP, Cutshall CD, Dale VH, et al. Road ecology: science and solutions. Washington, DC: Island Press; 2003.
- 3. Marsh DM, Milam GS, Gorham NA, Beckman NG. Forest roads as partial barriers to terrestrial salamander movement. Conserv Biol. 2005; 19: 2004–2008.
- 4. Grilo C, Bissonette JA, Santos-Reis M. Spatial–temporal patterns in Mediterranean carnivore road casualties: Consequences for mitigation. Biol Conserv. 2009; 142: 301–313.
- 5. McGregor RL, Bender DJ, Fahrig L. Do small mammals avoid roads because of the traffic? J Appl Ecol. 2008; 45: 117–123.
- 6. Macpherson D, Macpherson JL, Morris P. Rural roads as barriers to the movements of small mammals. Appl Ecol Environ Res. 2011; 9: 167–180.
- 7. Roedenbeck IA, Voser P. Effects of roads on spatial distribution, abundance and mortality of brown hare (Lepus europaeus) in Switzerland. Eur J Wildl Res. 2008; 54: 425–437.
- 8. Balkenhol N, Waits LP. Molecular road ecology: exploring the potential of genetics for investigating transportation impacts on wildlife. Mol Ecol. 2009; 18: 4151–4164. pmid:19732335
- 9. Holderegger R, Di Giulio M. The genetic effects of roads: A review of empirical evidence. Basic Appl Ecol. 2010; 11: 522–531.
- 10. Reed DH, Nicholas AC, Stratton GE. Genetic quality of individuals impacts population dynamics. Anim Conserv. 2007; 10: 275–283.
- 11. Saccheri I, Kuussaari M, Kankare M, Vikman P, Fortelius W, Hanski I. Inbreeding and extinction in a butterfly metapopulation. Nature. 1998; 392: 491–494.
- 12. Westemeier RL, Brawn JD, Simpson SA, Esker TL, Jansen RW, Walk JW, et al. Tracking the long-term decline and recovery of an isolated population. Science. 1998; 282: 1695–1698. pmid:9831558
- 13. Reijnen R, Foppen R, Braak CT, Thissen J. The effects of car traffic on breeding bird populations in woodland. III. Reduction of density in relation to the proximity of main roads. J Appl Ecol. 1995; 32: 187–202.
- 14. Jaeger JAG, Bowman J, Brennan J, Fahrig L, Bert D, Bouchard J, et al. Predicting when animal populations are at risk from roads: an interactive model of road avoidance behavior. Ecol Model. 2005; 185: 329–348.
- 15. Thurfjell H, Spong G, Olsson M, Ericsson G. Avoidance of high traffic levels results in lower risk of wild boar-vehicle accidents. Landscape Urban Plan. 2015; 133: 98–104.
- 16. Oxley DJ, Fenton MB, Carmody GR. The effects of roads on populations of small mammals. J Appl Ecol. 1974; 11: 51–59.
- 17. Goosem M. Effects of tropical rainforest roads on small mammals: inhibition of crossing movements. Wildlife Res. 2001; 28: 351–364.
- 18. McDonald WR, Clair CC. The effects of artificial and natural barriers on the movement of small mammals in Banff National Park, Canada. Oikos. 2004; 105: 397–407.
- 19. McLaren AAD, Fahrig L, Waltho N. Movement of small mammals across divided highways with vegetated medians. Can J Zool. 2011; 89: 1214–1222.
- 20. Brehme CS, Tracey JA, McClenaghan LR, Fisher RN. Permeability of roads to movement of scrubland lizards and small mammals. Conserv Biol. 2013; 27: 710–720. pmid:23772966
- 21. Gerlach G, Musolf K. Fragmentation of landscape as a cause for genetic subdivision in bank voles. Conserv Biol. 2000; 14: 1066–1074.
- 22. Gauffre B, Estoup A, Bretagnolle V, Cosson JF. Spatial genetic structure of a small rodent in a heterogeneous landscape. Mol Ecol. 2008; 17: 4619–4629. pmid:19140985
- 23. Rico A, Kindlmann P, Sedláček F. Can the barrier effect of highways cause genetic subdivision in small mammals? Acta Theriol. 2009; 54: 297–310.
- 24. Torre I, Arrizabalaga A, Díaz M. Ratón de campo (Apodemus sylvaticus Linnaeus, 1758). Galemys. 2002; 14: 1–26.
- 25. Rosalino LM, Santos-Reis M. Feeding habits of the common genet Genetta genetta (Carnivora: Viverridae) in a semi-natural landscape of central Portugal. Mammalia. 2002; 66: 195–206.
- 26. Tellería JL, Santos T, Alcántara M. Abundance and food-searching intensity of wood mice (Apodemus sylvaticus) in fragmented forests. J Mammal. 1991; 72: 183–187.
- 27. Gómez JM, Puerta-Piñero C, Schupp EW. Effectiveness of rodents as local seed dispersers of Holm oaks. Oecologia. 2008; 155: 529–537. pmid:18075760
- 28. Jaarsma CF, van Langevelde F, Botma H. Flattened fauna and mitigation: traffic victims related to road, traffic, vehicle, and species characteristics. Transport Res D-Tr E. 2006; 11: 264–276.
- 29. Gibbs JP, Shriver WG. Can road mortality limit populations of pool-breeding amphibians? Wetl Ecol Manag. 2005; 13: 281–289.
- 30. Alexander SM, Waters NM, Paquet PC. Traffic volume and highway permeability for a mammalian community in the Canadian Rocky Mountains. Can Geogr. 2005; 49: 321–331.
- 31. Landguth EL, Cushman SA, Schwartz MK, McKelvey KS, Murphy M, Luikart G. Quantifying the lag time to detect barriers in landscape genetics. Mol Ecol. 2010; 19: 4179–4191. pmid:20819159
- 32. Ascensão F, Clevenger AP, Grilo C, Filipe J, Santos-Reis M. Highway verges as habitat providers for small mammals in agrosilvopastoral environments. Biodivers Conserv. 2012; 21: 3681–3697.
- 33. Ruiz-Capillas P, Mata C, Malo JE. Road verges are refuges for small mammal populations in extensively managed Mediterranean landscapes. Biol Conserv. 2013; 158: 223–229.
- 34. Aronson J, Pereira JS, Pausas JG. Cork oak woodlands on the edge: ecology, adaptive management, and restoration. Washington, DC: Island Press; 2009.
- 35. Pinto-Correia T, Mascarenhas J. Contribution to the extensification/intensification debate: new trends in the Portuguese montado. Landscape Urban Plan. 1999; 46: 125–131.
- 36. Rosalino LM, Ferreira D, Leitão I, Santos-Reis M. Usage patterns of Mediterranean agro-forest habitat components by wood mice Apodemus sylvaticus. Mamm Biol. 2011; 76: 268–273.
- 37. Gonçalves P, Alcobia S, Simões L, Santos-Reis M. Effects of management options on mammal richness in a Mediterranean agro-silvo-pastoral system. Agroforest Syst. 2012; 85: 383–395.
- 38. Corp N, Gorman ML, Speakman JR. Ranging behaviour and time budgets of male wood mice Apodemus sylvaticus in different habitats and seasons. Oecologia. 1997; 109: 242–250.
- 39. Richardson JH, Shore RF, Treweek JR, Larkin SBC. Are major roads a barrier to small mammals? J Zool. 1997; 243: 840–846.
- 40. Underhill JE. Roads and wildlife: a study of the effects of roads on mammals in roadside habitats. PhD Thesis, University of Birmingham. 2002.
- 41. Seutin G, White BN, Boag PT. Preservation of avian blood and tissue samples for DNA analyses. Can J Zool. 1991; 69: 82–90.
- 42. Harr B, Musolf K, Gerlach G. Characterization and isolation of DNA microsatellite primers in wood mice (Apodemus sylvaticus, Rodentia). Mol Ecol. 2000; 9: 1664–1665. pmid:11050563
- 43. Makova KD, Patton JC, Krysanov EY, Chesser RK, Baker RJ. Microsatellite markers in wood mouse and striped field mouse (genus Apodemus). Mol Ecol. 1998; 7: 247–249. pmid:9532763
- 44. Wu H, Zhan X-J, Yan L, Liu S-Y, Li M, Hu J-C, et al. Isolation and characterization of fourteen microsatellite loci for striped field mouse (Apodemus agrarius). Conserv Genet. 2008; 9: 1691–1693.
- 45. Gu X-D, Liu S-Y, Wang Y-Z, Wu H. Development and characterization of eleven polymorphic microsatellite loci from South China field mouse (Apodemus draco). Conserv Genet. 2009; 10: 1961–1963.
- 46. Matschiner M, Salzburger W. TANDEM: integrating automated allele binning into genetics and genomics workflows. Bioinformatics. 2009; 25: 1982–1983. pmid:19420055
- 47. Rousset F. Genepop’007: a complete re-implementation of the Genepop software for Windows and Linux. Mol Ecol Resour. 2008; 8: 103–106. pmid:21585727
- 48. Holm S. A simple sequentially rejective multiple test procedure. Scand J Stat. 1979; 6: 65–70.
- 49. Van Oosterhout C, Hutchinson WF, Wills DPM, Shipley P. MICRO-CHECKER: software for identifying and correcting genotyping errors in microsatellite data. Mol Ecol Notes. 2004; 4: 535–538.
- 50. Kalinowski ST, Taper ML. Maximum likelihood estimation of the frequency of null alleles at microsatellite loci. Conserv Genet. 2006; 7: 991–995.
- 51. Belkhir K, Borsa P, Chikhi L, Raufaste N, Bonhomme F. GENETIX 4.05, logiciel sous Windows TM pour la génétique des populations. Laboratoire Génome, Populations, Interactions, CNRS UMR 5000, Université de Montpellier II. 1996–2004. Available: http://kimura.univ-montp2.fr/genetix/
- 52. Peakall R, Smouse PE. GENALEX 6: genetic analysis in Excel. Population genetic software for teaching and research. Mol Ecol Notes. 2006; 6: 288–295.
- 53. Peakall R, Smouse PE. GenAlEx 6.5: genetic analysis in Excel. Population genetic software for teaching and research—an update. Bioinformatics. 2012; 28: 2537–2539. pmid:22820204
- 54. Queller DC, Goodnight KF. Estimating relatedness using genetic markers. Evolution. 1989; 43: 258–275.
- 55. Ryman N, Palm S. POWSIM: a computer program for assessing statistical power when testing for genetic differentiation. Mol Ecol Notes. 2006; 6: 600–602.
- 56. Anderson CD, Epperson BK, Fortin MJ, Holderegger R, James P, Rosenberg MS, et al. Considering spatial and temporal scale in landscape-genetic studies of gene flow. Mol Ecol. 2010; 19: 3565–3575. pmid:20723051
- 57. Blair C, Weigel DE, Balazik M, Keeley ATH, Walker FM, Landguth E, et al. A simulation-based evaluation of methods for inferring linear barriers to gene flow. Mol Ecol Resour. 2012; 12: 822–833. pmid:22551194
- 58. Goudet J, Raymond M, de Meeus T, Rousset F. Testing differentiation in diploid populations. Genetics. 1996; 144: 1933–1940. pmid:8978076
- 59. De Meeûs T, Guégan J-F, Teriokhin AT. MultiTest V.1.2, a program to binomially combine independent tests and performance comparison with other related methods on proportional data. BMC Bioinformatics. 2009; 10: 443. pmid:20030807
- 60. Weir BS, Cockerham CC. Estimating F-Statistics for the analysis of population structure. Evolution. 1984; 38: 1358–1370.
- 61. Meirmans PG, Hedrick PW. Assessing population structure: FST and related measures. Mol Ecol Resour. 2011; 11: 5–18. pmid:21429096
- 62. Jost L. GST and its relatives do not measure differentiation. Mol Ecol. 2008; 17: 4015–4026. pmid:19238703
- 63. Meirmans PG, Van Tienderen PH. GENOTYPE and GENODIVE: two programs for the analysis of genetic diversity of asexual organisms. Mol Ecol Notes. 2004; 4: 792–794.
- 64. Chapuis M-P, Estoup A. Microsatellite null alleles and estimation of population differentiation. Mol Biol Evol. 2007; 24: 621–631. pmid:17150975
- 65. Cavalli-Sforza LL, Edwards AWF. Phylogenetic analysis. Models and estimation procedures. Am J Hum Genet. 1967; 19: 233–257. pmid:6026583
- 66. Goldberg CS, Waits LP. Quantification and reduction of bias from sampling larvae to infer population and landscape genetic structure. Mol Ecol Resour. 2010; 10: 304–313. pmid:21565025
- 67. Marsh DM, Page RB, Hanlon TJ, Bareke H, Corritone R, Jetter N, et al. Ecological and genetic evidence that low-order streams inhibit dispersal by red-backed salamanders (Plethodon cinereus). Can J Zool. 2007; 85: 319–327.
- 68. Marsh DM, Page RB, Hanlon TJ, Corritone R, Little EC, Seifert DE, et al. Effects of roads on patterns of genetic differentiation in red-backed salamanders, Plethodon cinereus. Conserv Genet. 2008; 9: 603–613.
- 69. Kimura M, Ohta T. Stepwise mutation model and distribution of allelic frequencies in a finite population. P Natl Acad Sci USA. 1978; 75: 2868–2872.
- 70. Di Rienzo A, Peterson AC, Garza JC, Valdes AM, Slatkin M, Freimer NB. Mutational processes of simple-sequence repeat loci in human populations. P Natl Acad Sci USA. 1994; 91: 3166–3170.
- 71. Crow JF, Kimura M. An introduction to population genetics theory. 1970; Caldwell, NJ, USA: Blackburn Press.
- 72. Waples RS, Do C. LDNE: a program for estimating effective population size from data on linkage disequilibrium. Mol Ecol Resour. 2008; 8: 753–756. pmid:21585883
- 73. Dallas JF. Estimation of microsatellite mutation rates in recombinant inbred strains of mouse. Mamm Genome. 1992; 3: 452–456. pmid:1643307
- 74. Dietrich W, Katz H, Lincoln SE, Shin HS, Friedman J, Dracopoli NC, et al. A genetic-map of the mouse suitable for typing intraspecific crosses. Genetics. 1992; 131: 423–447. pmid:1353738
- 75. Tallmon DA, Draheim HM, Mills LS, Allendorf FW. Insights into recently fragmented vole populations from combined genetic and demographic data. Mol Ecol. 2002; 11: 699–709. pmid:11972758
- 76. Wilensky U. NetLogo. http://ccl.northwestern.edu/netlogo/. Center for Connected Learning and Computer-Based Modeling. Northwestern University. Evanston, IL. 1999.
- 77. Balloux F. EASYPOP (version 1.7): a computer program for population genetics simulations. J Hered. 2001; 92: 301–302. pmid:11447253
- 78. Bonin A, Bellemain E, Bronken Eidesen P, Pompanon F, Brochmann C, Taberlet P. How to track and assess genotyping errors in population genetics studies. Mol Ecol. 2004; 13: 3261–3273. pmid:15487987
- 79. Hoffman JI, Amos W. Microsatellite genotyping errors: detection approaches, common sources and consequences for paternal exclusion. Mol Ecol. 2005; 14: 599–612. pmid:15660949
- 80. Pompanon F, Bonin A, Bellemain E, Taberlet P. Genotyping errors: causes, consequences and solutions. Nat Rev Genet. 2005; 6: 847–859. pmid:16304600
- 81. Selkoe KA, Toonen RJ. Microsatellites for ecologists: a practical guide to using and evaluating microsatellite markers. Ecol Lett. 2006; 9: 615–629. pmid:16643306
- 82. Carlsson J. Effects of microsatellite null alleles on assignment testing. J Hered. 2008; 99: 616–623. pmid:18535000
- 83. Berckmoes V, Scheirs J, Jordaens K, Blust R, Backeljau T, Verhagen R. Effects of environmental pollution on microsatellite DNA diversity in wood mouse (Apodemus sylvaticus) populations. Environ Toxicol Chem. 2005; 24: 2898–2907. pmid:16398127
- 84. Booth W, Montgomery WI, Prodöhl PA. Spatial genetic structuring in a vagile species, the European wood mouse. J Zool. 2009; 279: 219–228.
- 85. Leng L, Zhang D-X. Measuring population differentiation using GST or D? A simulation study with microsatellite DNA markers under a finite island model and nonequilibrium conditions. Mol Ecol. 2011; 20: 2494–2509. pmid:21557781
- 86. Ryman N, Leimar O. GST is still a useful measure of genetic differentiation—a comment on Jost's D. Mol Ecol. 2009; 18: 2084–2087. pmid:19389168
- 87. Leng L, Zhang D-X. Time matters: Some interesting properties of the population differentiation measures GST and D overlooked in the equilibrium perspective. J Syst Evol. 2013; 51: 44–60.
- 88. Lalis A, Leblois R, Liefried S, Ouarour A, Beeravolu CR, Michaux J, et al. New molecular data favour an anthropogenic introduction of the wood mouse (Apodemus sylvaticus) in North Africa. J Zool Syst Evol Res. 2016; 54: 1–12.
- 89. Keller I, Nentwig W, Largiader CR. Recent habitat fragmentation due to roads can lead to significant genetic differentiation in an abundant flightless ground beetle. Mol Ecol. 2004; 13: 2983–2994. pmid:15367114
- 90. Crawley MC. Movements and home-ranges of Clethrionomys glareolus Schreber and Apodemus sylvaticus L. in north-east England. Oikos. 1969; 20: 310–319.
- 91. Watts CHS. Long distance movement of Bank voles and Wood mice. J Zool. 1970; 161: 247–256.
- 92. Dickman CR, Doncaster CP. The ecology of small mammals in urban habitats. II. Demography and dispersal. J Anim Ecol. 1989; 58: 119–127.
- 93. Zhang Z, Usher MB. Dispersal of wood mice and bank voles in an agricultural landscape. Acta Theriol. 1991; 36: 239–245.
- 94. Hacker HP, Pearson HS. Distribution of the long-tailed field mouse, Apodemus sylvaticus, on South Haven Peninsula, Dorset, in 1937, with some observations on its wandering and homing powers. J Linn Soc Zool. 1951; 42: 1–17.
- 95. Wolton RJ. The ranging and nesting behaviour of Wood mice, Apodemus sylvaticus (Rodentia: Muridae), as revealed by radio-tracking. J Zool. 1985; 206: 203–222.
- 96. Wright S. Isolation by distance. Genetics. 1943; 28: 114–138. pmid:17247074
- 97. Wilson A, Fenton B, Malloch G, Boag B, Hubbard S, Begg G. Urbanisation versus agriculture: a comparison of local genetic diversity and gene flow between wood mouse Apodemus sylvaticus populations in human-modified landscapes. Ecography. 2016; 39: 87–97.
- 98. Dolan L. Monitoring of wildlife crossing structures on Irish national road schemes. In: Irwin CL, Garrett P, McDermott KP, editors. Proceedings of the 2005 International Conference on Ecology and Transportation. Raleigh, NC: Center for Transportation and the Environment, North Carolina State University; 2006. p. 608 (Abstract).
- 99. Lode T. Effect of a motorway on mortality and isolation of wildlife populations. Ambio. 2000; 29: 163–166.
- 100. Van Wieren SE, Worm PB. The use of a motorway wildlife overpass by large mammals. Neth J Zool. 2001; 51: 97–105.
- 101. Tew TE, Macdonald DW. The effects of harvest on arable wood mice Apodemus sylvaticus. Biol Conserv. 1993; 65: 279–283.
- 102. Charlesworth B. Measures of divergence between populations and the effect of forces that reduce variability. Mol Biol Evol. 1998; 15: 538–543. pmid:9580982
- 103. Nagylaki T. Fixation indices in subdivided populations. Genetics. 1998; 148: 1325–1332. pmid:9539445
- 104. Hedrick PW. Perspective: highly variable loci and their interpretation in evolution and conservation. Evolution. 1999; 53: 313–318.
- 105. Orłowski G, Nowak L. Factors influencing mammal roadkills in the agricultural landscape of south-western Poland. Pol J Ecol. 2006; 54: 283–294.
- 106. Borkovcová M, Mrtka J, Winkler J. Factors affecting mortality of vertebrates on the roads in the Czech Republic. Transport Res D-Tr E. 2012; 17: 66–72.
- 107. Epps CW, Palsbøll PJ, Wehausen JD, Roderick GK, Ramey RR II, McCullough DR. Highways block gene flow and cause a rapid decline in genetic diversity of desert bighorn sheep. Ecol Lett. 2005; 8: 1029–1038.
- 108. Waples RS. A bias correction for estimates of effective population size based on linkage disequilibrium at unlinked gene loci. Conserv Genet. 2006; 7: 167–184.
- 109. Waples RS, Do C. Linkage disequilibrium estimates of contemporary Ne using highly variable genetic markers: a largely untapped resource for applied conservation and evolution. Evol Appl. 2010; 3: 244–262. pmid:25567922
- 110. Waples RS, England PR. Estimating contemporary effective population size on the basis of linkage disequilibrium in the face of migration. Genetics. 2011; 189: 633–644. pmid:21840864
- 111. Waples RS. Genetic estimates of contemporary effective population size: to what time periods do the estimates apply?. Mol Ecol. 2005; 14: 3335–3352. pmid:16156807
- 112. Waples RS, Antao T, Luikart G. Effects of overlapping generations on linkage disequilibrium estimates of effective population size. Genetics. 2014; 197: 769–780. pmid:24717176
- 113. Watts CHS. The regulation of wood mouse (Apodemus sylvaticus) numbers in Wytham woods, Berkshire. J Anim Ecol. 1969; 38: 285–304.
- 114. Kalinowski ST, Waples RS. Relationship of effective to census size in fluctuating populations. Conserv Biol. 2002; 16: 129–136.
- 115. Waples RS. Effective size of fluctuating salmon populations. Genetics. 2002; 161: 783–791. pmid:12072473
- 116. Chakraborty R, Danker-Hopfe H. Analysis of population structure: a comparative study of different estimators of Wright’s fixation indices. In: Rao CR, Chakraborty R, editors. Handbook of Statistics 8, Statistical Methods in Biological and Medical Sciences. Amsterdam: Elsevier Science Publishers; 1991. pp. 203–254.
- 117. Kalinowski ST. Do polymorphic loci require large sample sizes to estimate genetic distances?. Heredity. 2005; 94: 33–36. pmid:15329660
- 118. Riley SPD, Pollinger JP, Sauvajot RM, York EC, Bromley C, Fuller TK, et al. A southern California freeway is a physical and social barrier to gene flow in carnivores. Mol Ecol. 2006; 15: 1733–1741. pmid:16689893
- 119. DiLeo MF, Rouse JD, Dávila JA, Lougheed SC. The influence of landscape on gene flow in the eastern massasauga rattlesnake (Sistrurus c. catenatus): insight from computer simulations. Mol Ecol. 2013; 22: 4483–4498. pmid:23889682
- 120. Wright S. Evolution in Mendelian populations. Genetics. 1931; 16: 97–159. pmid:17246615
- 121. Mills LS, Allendorf FW. The one-migrant-per-generation rule in conservation and management. Conserv Biol. 1996; 10: 1509–1518.
- 122. Vucetich JA, Waite TA. Is one migrant per generation sufficient for the genetic management of fluctuating populations?. Anim Conserv. 2000; 3: 261–266.
- 123. Wang J. Application of the one-migrant-per-generation rule to conservation and management. Conserv Biol. 2004; 18: 332–343.
- 124. MacDonald D, Barrett P. Mammals of Britain & Europe (Collins Field Guide). London: HarperCollinsPublishers; 1993.
- 125. Butet A, Paillat G. Insectivores et rongeurs de France: le Mulot sylvestre–Apodemus sylvaticus (Linné, 1758). Arvicola. 1997; 9: 7–23.
- 126. Hacker HP, Pearson HS. The Growth, Survival, Wandering and Variation of the Long-Tailed Field Mouse, Apodemus Sylvaticus. Biometrika. 1946; 33: 333–361.
- 127. Gibson DSC, Delany MJ. The population ecology of small rodents in Pennine woodlands. J Zool. 1984; 203: 63–85.
- 128. Moreno S, Kufner MB. Seasonal patterns in the wood mouse population in Mediterranean scrubland. Acta Theriol. 1988; 33: 79–85.
- 129. Tkadlec E, Zejda J. Small rodent population fluctuations: the effects of age structure and seasonality. Evol Ecol. 1998; 12: 191–210.
- 130. Jones KE, Bielby J, Cardillo M, Fritz SA, O'Dell J, Orme CDL, et al. PanTHERIA: a species-level database of life history, ecology, and geography of extant and recently extinct mammals: Ecological Archives E090-184. Ecology. 2009; 90: 2648.
- 131. Pergams ORW, Ashley MV. Microevolution in island rodents. Genetica. 2001; 112–113: 245–256. pmid:11838768
- 132. Bengtson S-A, Nilsson A, Nordström S, Rundgren S. Body weights of Apodemus sylvaticus in Iceland. Acta Theriol. 1976; 21: 389–399.
- 133. Halle S. Wood mice (Apodemus sylvaticus L.) as pioneers of recolonization in a reclaimed area. Oecologia. 1993; 94: 120–127.
- 134. Rosário IT, Mathias ML. Annual weight variation and reproductive cycle of the wood mouse (Apodemus sylvaticus) in a Mediterranean environment. Mammalia. 2004; 68: 133–140.
- 135. Green R. The ecology of wood mice (Apodemus sylvaticus) on arable farmland. J Zool. 1979; 188: 357–377.
- 136. Ashby KR. Studies on the ecology of field mice and voles (Apodemus sylvaticus, Clethrionomys glareolus and Microtus agrestis) in Houghall Wood, Durham. J Zool. 1967; 152: 389–513.
- 137. Smal CM, Fairley JS. The dynamics and regulation of small rodent populations in the woodland ecosystems of Killarney, Ireland. J Zool. 1982; 196: 1–30.
- 138. Díaz M, Torre I, Arrizabalaga A. Relative roles of density and rainfall on the short-term regulation of Mediterranean wood mouse Apodemus sylvaticus populations. Acta Theriol. 2010; 55: 251–260.
- 139. Kikkawa J. Movement, activity and distribution of the small rodents Clethrionomys glareolus and Apodemus sylvaticus in woodland. J Anim Ecol. 1964; 33: 259–299.
- 140. Montgomery WI. Population regulation in the wood mouse, Apodemus sylvaticus. II. Density dependence in spatial distribution and reproduction. J Anim Ecol. 1989; 58: 477–494.
- 141. Ruiz-Capillas P, Mata C, Malo JE. How many rodents die on the road? Biological and methodological implications from a small mammals’ roadkill assessment on a Spanish motorway. Ecol Res. 2015; 30: 417–427.
- 142. Jackson ND, Fahrig L. Relative effects of road mortality and decreased connectivity on population genetic diversity. Biol Conserv. 2011; 144: 3143–3148.
- 143. Finnegan LA, Wilson PJ, Price GN, Lowe SJ, Patterson BR, Fortin M-J, et al. The complimentary role of genetic and ecological data in understanding population structure: a case study using moose (Alces alces). Eur J Wildl Res. 2012; 58: 415–423.
- 144. Fedy BC, Martin K, Ritland C, Young J. Genetic and ecological data provide incongruent interpretations of population structure and dispersal in naturally subdivided populations of white-tailed ptarmigan (Lagopus leucura). Mol Ecol. 2008; 17: 1905–1917. pmid:18363666
- 145. Kozakiewicz M. Habitat isolation and ecological barriers—the effect on small mammal populations and communities. Acta Theriol. 1993; 38: 1–30.
- 146. Yanes M, Velasco JM, Suárez F. Permeability of roads and railways to vertebrates: the importance of culverts. Biol Conserv. 1995; 71: 217–222.
- 147. Mata C, Hervás I, Herranz J, Suárez F, Malo JE. Complementary use by vertebrates of crossing structures along a fenced Spanish motorway. Biol Conserv. 2005; 124: 397–405.
- 148. Clevenger AP, Chruszcz B, Gunson K. Drainage culverts as habitat linkages and factors affecting passage by mammals. J Appl Ecol. 2001; 38: 1340–1349.
- 149. Clark RW, Brown WS, Stechert R, Zamudio KR. Roads, interrupted dispersal, and genetic diversity in timber rattlesnakes. Conserv Biol. 2010; 24: 1059–1069. pmid:20151984
- 150. Ascensão F. Mira A. Spatial patterns of road kills: a case study in Southern Portugal. In: Irwin CL, Garrett P, McDermott KP, editors. Proceedings of the 2005 International Conference on Ecology and Transportation. Raleigh, NC: Center for Transportation and the Environment, North Carolina State University; 2006. pp. 641–646 (Abstract).
- 151. McDonald W, Clair CC. Elements that promote highway crossing structure use by small mammals in Banff National Park. J Appl Ecol. 2004; 41: 82–93.
- 152. Encarnacão JA, Becker NI. Stealthy at the roadside: Connecting role of roadside hedges and copse for silvicolous, small mammal populations. J Nat Conserv. 2015; 27: 37–43.
- 153. Ascensão F, LaPoint S, van der Ree R. Roads, Traffic and Verges: Big Problems and Big Opportunities for Small Mammals. In: van der Ree R, Smith DJ, Grilo C, editors. Handbook of Road Ecology. Chichester, UK: John Wiley & Sons, Ltd; 2015. pp. 325–333.