Inferring inter-colony movement within metapopulations of yellow-footed rock-wallabies using estimates of kinship

Understanding the exchange of individuals between wildlife populations, particularly those with naturally fragmented habitats, is important for the effective management of these species. This is of particular consequence when the species is of conservation concern, and isolated populations may be lost due to pressures from predation or competition, or catastrophic events such as wildfire. Here we demonstrate the use kinship and population structure analysis to show potential recent movement between colonies in metapopulations of yellow-footed rock-wallaby (Petrogale xanthopus Gray 1854) at two sites in the Grey Range of Queensland, and at four sites in the Gawler Ranges of South Australia. These colonies are also compared to a single colony from the Flinders Ranges, a connected landscape of rock-wallaby habitat. Using reduced representation next-generation sequencing, we acquired and filtered a set of ~ 17,000 single-nucleotide polymorphisms to examine population genetic variation, structure and relationships within populations, and also identify putative migrants. Initial STRUCTURE analysis re-confirmed each population should be considered separately. Tests of population genetic variation identify several colonies appearing to be experiencing genetic erosion, also with low calculated effective population sizes (Ne = 4.5–36.6). Pairwise comparisons of individual relatedness (relatedness coeffiecients; r) implied several contemporary movement events between colonies within both the Gawler and Grey Ranges (r > 0.125), which was then affirmed with tests for putative first generation migrants. These results are of particular note in South Australia, where threat abatement (management of key predators and competitors) may facilitate dispersion. Additionally, in Queensland, colonies are separated by anthropogenic barriers: predator exclusion fencing designed to exclude dingoes (Canis familiaris) from grazing land, which may hinder dispersal. This work highlights the usefulness of population genetics to inform management outcomes in wildlife, in this case, highlighting the need for threatened species management at the landscape level.


Introduction
A metapopulation is the group of spatially distinct populations of the same species connected by movement of individuals (Wells and Richmond 1995). For species in such systems, movement behaviours are essential, as they insure against risk of extinction from negative pressures (such as predation, competition and catastrophic events; Holyoak and Lawler 1996), and protect against the negative genetic effects of inbreeding (Olivieri et al. 1995;Perrin and Mazalov 1999). Movement behaviour also gives rise to potential recolonization of "empty" sites or the formation of new populations at suitable sites (Hanski 1998). Understanding such movement is therefore critical for effective species management.

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For timid and reclusive species, it can be hard to determine whether individuals are moving between isolated colonies. In these species, the use of genetic techniques to identify the relationships between individuals of a population could be used to infer recent movement events, and be extremely useful to understanding barriers to dispersal (Escoda et al. 2019).
The yellow-footed rock-wallaby (Petrogale xanthopus Gray, 1854) is a threatened macropod found in the semiarid zone of Australia. There are two subspecies of P. xanthopus: P. x. xanthopus is found in several remote mountain ranges of South Australia (SA; Threatened Species Scientific Committee 2016a), and also a single population in New South Wales (NSW; Lim and Giles 1987), and P. x. celeris is found in the Grey Range in Queensland (QLD; Threatened Species Scientific Committee 2016b). The distribution of both subspecies is assumed to have significantly decreased since European settlement (Copley 1983). Rock-wallabies (Petrogale spp.) have high habitat specificity, only occupying complex rocky habitats (see Gordon et al. 1993;Lim and Giles 1987;Smith and Allen 2021;Telfer et al. 2008). As a result of this habitat specificity, suitable rock-wallaby habitat is naturally fragmented, forming metapopulations (Lethbridge et al. 2019;Lethbridge and Strauss 2015;Murray et al. 2008;Ruykys and Lancaster 2015). Primary evidence of movement between colonies of P. xanthopus is surprisingly scarce given the quantity of literature describing the species, particularly in South Australia, though it is not completely absent. A study using tracking collars and earmarked rock-wallabies in Queensland found evidence of a single movement event over 36 months (Sharp 2002), and another (also with collars) revealed several long distance transient movements of released captive-bred rock-wallabies (Lapidge 2001). The latter also inferred several dispersal events from wild rock-wallabies that were trapped at the previously empty reintroduction sites.
The limitations of radio tracking and capture-markrecapture to detect all movement behaviours is evidentboth rely on the captured individual moving during the study period. In addition to this, the ability to detect or recapture individuals that have moved is further limited by the distance of the movement. Detecting long distance movements, such as natal dispersal, with such techniques is understandably infrequent for P. xanthopus. The use of genetic data would mitigate both these shortcomings, as it would detect any contemporary movement event between colonies at any distance, as long as two related individuals are sampled. To this end, a recent study assessing the genetic variation of P. x. xanthopus identified 13 putative first generation migrations of between 2 and 60 km over connected habitat in the Flinders ranges using population assignment methods based on the individuals' genetic structure gained through microsatellite analysis (n = 194, Potter et al. 2020). Potter et al. (2020) built on earlier genetic analysis of dispersal (also using microsatellite analysis), that had concluded that yellow-footed rock-wallabies rarely move between colonies, even within connected habitat (Pope et al. 1996), although the methods employed were reliable, this earlier study was limited by sample size. Advancements in genetic technologies such as next-generation sequencing (NGS), and the development of more robust methods of determining kinship values also provides greater confidence in the results of kinship analysis. This confidence can allow for more reliable inferences to be drawn between kinship values and the probability of a contemporary movement between colonies (Escoda et al. 2017). These early P. xanthopus studies were also performed without or with limited threat abatement practices (effective management of key predators and feral competitors) in place, which may be critical to allow rock-wallaby movement behaviours (Pope et al. 1996(Pope et al. , 1998. While the recent publications on the same species are highly informative, a greater understanding of P. xanthopus inter-colony movement is needed to understand potential metapopulation dynamics for the purpose of informing management of the species. The distribution of P. x. celeris has recently (2016) been heavily subdivided by agricultural exclusion fences (Smith et al. 2020c). While the fences may ultimately be of a benefit to the species' long term persistence (Smith et al. 2020c), exclusion fencing has the potential to isolate colonies, which may lead to genetic consequences (Smith et al. 2020a, b, c). The conservation of P. x. xanthopus may also be reliant on an understanding of inter-colony relations and connectivity. Predation from red foxes (Vulpes vulpes), competition with feral goats (Capra hircus) and catastrophes can all contribute to extinction risk of the entire metapopulation by restricting dispersal behaviours between colonies. Understanding the interchange of the individuals between sites would give insight into the effect of pest species control on metapopulation dynamics and the utility of broad scale pest management in the effective conservation of P. xanthopus.
Given the cryptic nature of the species, its disjunct distribution, and threats facing both subspecies, here we use P. xanthopus to demonstrate the usefulness of reduced representation next-generation sequencing to study metapopulation movement, population structure and how outcomes from such studies can help inform threatened species management. Our objective is to assess if there has been recent movement of P. xanthopus between geographically distinct colonies, using population structure analysis, pairwise relatedness coefficients and identification of first-generation migrants. We then discuss the value of kinship analysis to infer species movement within potential metapopulations, and how this analysis affects the management of P. xanthopus, both in South Australia and Queensland.

Study sites
Petrogale xanthopus were trapped and ear biopsies were obtained at four sites in the Gawler Ranges, and one site in the Flinders Ranges (South Australia) by Lethbridge and Andrews (2014) and later Lethbridge (unpublished report), under a S.A. Wildlife Ethics approval: S23997-19, and at two sites in the Grey Range, near Quilpie in central-western Queensland, under a University of Southern Queensland Animal Ethics approval: USQ-17REA011 (Fig. 1). The Gawler Ranges (GWL), the Flinders Ranges (FLD) and the Grey Range (GRY) will hereafter be referred to as 'populations'. Trapping sites within populations will be referred to as 'colonies'. Trapping in the Flinders and Gawler Ranges (South Australia) took place from August 2012 to September 2016, and in the Grey Range (Queensland) in 2018 and 2019. The two colonies in Queensland are separated by 8 km, including approximately 5 km of unsuitable habitat. Historically this gap between the two colonies was thought to be traversable by P. xanthopus, but an exclusion fence was erected 2 years prior to sampling to alleviate the pressures of wild dog predation on sheep grazing properties. The colonies in the Gawler Ranges are not disrupted by fencing but vary in distance from Yandinga, a theorised source/refuge population (Fig. 1). The Gawler Ranges populations were also historically disrupted by exclusion fencing (circa 1920s), but spatial and temporal information on this fencing is minimal/non-existent.

Trapping, sampling, extraction and sequencing
Rock-wallabies were trapped using established methods in soft-walled treadle cage. A tissue biopsy was removed from each rock-wallaby's ear using a 3 mm punch. The sample is taken from the opposite ear to an ear-tag employed for potential future visual identification in the field. Morphometric data was also collected before each rock-wallaby was microchipped for identification on recapture. Tissue samples were placed in Longmire's buffer solution (Queensland samples- Longmire et al. 1997) or 100% ethanol (South Australian samples) and stored in a cool place until extraction. DNA was extracted from 95 samples (Table 1) using a salt-based ethanol extraction (Ebert and Andrew 2014) and quantified on a Qubit™ Flurometer and quality controlled using a NanoDrop™ 3000. One sample from the Flinders Ranges site was not of high enough quality for accurate sequencing (based on quality control steps) and therefore was removed from the samples sent for sequencing. Samples were then sent to Diversity Arrays Technology (DArT P/L) in Canberra, ACT for sequencing via their DArTseq service (Kilian et al. 2012). The protocol involves technical replicates, which provides an empirical measure of the repeatability of the resulting loci. DArT conducted filtering and reference-free clustering of reads, followed by genotyping using their proprietary analysis pipeline (see https:// www. diver sitya rrays. com). Three samples did not meet DArT's internal quality control thresholds, and therefore data was not returned for these samples.

Data filtering
The single-nucleotide polymorphism (SNP) data returned by DArT was first explored in R (version 3.6.2) using the dartR v1.1.11 package and following the workflow suggested in the package documentation (Gruber et al. 2019a, b). The reports generated by this initial analysis were used to inform filtering thresholds (Tables S1-S5, Figs. S1, S2). The primary dataset was later subdividedbased on population structure results. This was completed to look for hierarchical structuring (see Results) and for further analysis of kinship (see (v) Coefficients of relationship, relatedness networks). As these subsets reflect the source populations, these datasets were named after the population. The filtered, total dataset will be referred to as the primary dataset (Table 1). Monomorphic loci are automatically removed during this sub-setting. Data were first filtered for the average repeatability of each locus (loci with repeatability > 0.95 were kept), and the call rate by locus (> 0.95) and by individual (> 0.90).
The data was then filtered to remove over-split loci (< 0.2 Hamming distance), and for observed heterozygosity greater than 0.6. Finally, loci with minor allele frequencies lower than 0.05 were removed before all metrics were recalculated. Filtering thresholds were chosen based on the recommendations of Gruber et al. (2019b) and O'Leary et al. (2018).
Relatedness estimates range from 0 (totally unrelated individuals) to 1 (clones). Preliminary data exploration identified four samples with high pairwise relatedness to other samples, which is not consistent with outbreeding and random mating. These values may have arisen in a number of ways: monozygotic twinning, duplicate sampling or pipetting error prior to sequencing. Twins are known to occur in Petrogale assimilis (Spencer and Marsh 1997), and the twinning rate in Macropus is low, but non-zero (Inns 1980;Norbury 1986;van Oorschot and Cooper 1989). Additionally, pouch young have DNA samples taken, but are not ear tagged/microchipped and may have been sampled again as adults. Nevertheless, as pipetting error cannot be excluded, we removed samples with high pairwise kinship estimates prior to all analyses. The sample of higher quality was kept and the sample of lower quality was removed prior to filtering and final analysis.

Population structure, statistics, genetic distances, and PCoA
Population structure analysis was performed using STRU CTU RE (v2.3.4; Pritchard et al. 2000). Parameter settings varied by dataset. The primary dataset was first analysed from for all clusters (K) from 1 to 10, with 10 independent repeats of 100,000 MCMC (Markov Chain Monte Carlo) iterations after a 10,000 iteration burn-in. Based on these results, Datasets 2-4 (subsets of the primary dataset) were analysed, using more robust methods. Each dataset was analysed from K = 1-10, after 50,000 burn-in and 500,000 MCMC iterations with sampling populations as priori. K values were estimated through an assessment of both Pritchard's model likelihood method (Pritchard et al. 2000) and Evanno's ΔK method (Evanno et al. 2005) implemented in Structure Harvester (Earl and vonHoldt 2012), and scrutinised following recommendations detailed in Cullingham et al. (2020) for K = 2 results. The production of population structure bar plots was performed in CLUMPAK (v1.1; Kopelman et al. 2015). Also, Principle Coordinate Analysis (PCoA) was performed using Euclidean distance in R with dartR. Each dataset was analysed and informative dimensions examined. Plots of the two most informative axes of each population were generated with ggplot2 v3.3.2 (Wickham 2006). Mean observed heterozygosity (H O ), expected heterozygosity (H E ), population Allelic Richness (rarefied allelic counts, per locus and population; A R ), and inbreeding coefficients (F IS ) were reported using hierfstat v0.04-22 in R (basic.stats function) with 98% confidence intervals (1000 bootstraps). Population divergence was explored using several approaches; pairwise private and fixed alleles, Euclidean and Nei's (Nei 1972) genetic distance matrices as well as pairwise F ST . Pairwise F ST values were also estimated using StAMPP (1000 bootstraps, 95% CI), which follows Weir and Cockerham's (Weir and Cockerham 1984) methods. An unrooted neighbour joining tree was constructed from a Euclidian distance matrix before effective population sizes ( N e ) were estimated for each colony using NeEstimator (v2.1; Do et al. 2014) using the Linkage Disequilibrium (random mating) methods for a minimum allele frequency at 0.05, 0.02 and 0.01 with jack-knife confidence intervals (Jones et al. 2016).

Coefficients of relationship, relatedness networks
The R package SNPRelate v1.16.0 (Zheng 2013) was first used to calculate Identity-By-State (IBS) fractions for each pair of rock-wallabies in each of the Datasets 1-4. Hierarchical cluster analysis using the average link (UPGMA) method was then performed on each of the IBS matrices to produce a genetic distance trees. Kinship was estimated independently in Datasets 2-4, to ensure that later filtering was not biased by sample size, and that appropriate population-specific allele frequencies were used. The primary dataset contains SNPs that are monomorphic in individual populations and kinship values can be inflated by these fixed alleles. Identity-By-Descent coefficients (calculated by Maximum Likelihood Estimation) were estimated in R using the SNPRelate package (Zheng 2013). Pairwise kinship values were estimated based on these IBD coefficients, also using SNPRelate. Kinship values vary from 0 to 0.5 so, for ease of comprehension, coefficients of relationship (r), which vary from 0 to 1, were calculated by doubling kinship values (Wright 1922). Full siblings and parent-offspring pairs are expected to have r values of approximately 0.5, half siblings 0.25, and first cousins 0.125, and so on. To visualise close r values geographically, the program GEPHI (v0.9.2; Bastian, Heymann and Jacomy, 2009) was used to produce relatedness networks with the plugin GeoLayout. Individuals were treated as nodes and relatedness estimates as edge values, weighted by increasing r. These visualisations were limited to coefficients of relationship greater than 0.0625 (i.e. 1/16th, e.g. first-cousin once removed, half-first-cousin).

First-generation migration
GeneClass2 (Piry et al. 2004) was used to identify presumed first generation (f 0 ) migrants. This was performed using the Rannala and Mountain (1997) methods with Monte-Carlo resampling at both the 0.01 and 0.05 probability threshold and all loci. This approach follows the same methods as Potter et al. (2020). The distance between the trapping (source) colony and the putative origin colony (as well as the site map, Fig. 1) was also then generated in ArcMap (v10.5.1; Environmental Systems Research Institute 2019).

Population structure, statistics, genetic distances, and PCoA
The Gawler sites (Coolgundibie, Organ Pipes, Stone Dam and Yandinga) consistently had the lowest observed and expected heterozygosity (H O and H E , respectively), followed by the Gray Range population and Flinders Ranges sites (  (Table 2). These results were also reflected in the results of allelic richness, which was highest within the Flinders Ranges colony, followed by the Grey Range and finally Gawler Ranges (Table 2). Pairwise F ST was greatest between the Coolgundibie and Ray colonies, and the lowest value was between the geographically nearby Yandinga and Organ Pipes colonies (Table 3) Table 3).
The neighbour-joining tree clearly separates colonies by population (Fig. 2). This was also evident using several other different genetic distance measures (Supplementary Information), as well as through Principal Coordinates Analysis (Fig. 3). The first two eigenvalues in the PCoA of the primary dataset corresponded to 47.1% and 12.0% (Fig. S5) of the variation between samples.
Effective population size (N e ) estimates ranged from 4.5 for the Stone Dam colony, to 36.6 for the Yandinga colony in the Gawler Ranges. In the Flinders Ranges, the Waukawoodna Gap colony had an N e of 21.4, and in the Grey Range, the Ray and Alaric colonies had N e estimates of 5.1 and 21.3, respectively (Table 2).
After STRU CTU RE analysis, Evanno's ΔK method from STRU CTU RE HARVESTER indicated that K = 2 was the best supported K value for the primary dataset 1; however, the maximum L(K), pairwise F ST values (Table 3), neighbour-joining trees (Fig. 2), genetic distances (Table S7-10), PCoA results (Fig. 3) and other analyses all gave K = 3 greater support. Therefore, delimitations of K = 3 (Fig. 4) were used to subset the primary dataset into populations for further investigation of hierachical population structure and kinship analysis.
PCoA analysis of the Gawler ranges showed some potential structure (Fig. 3) though the percentage contributions of each axis to differentiation were relatively low (Supplementary Information). Genetic distance trees showed little structure. Bayesian cluster analysis with STRU CTU RE showed the greatest support for K = 2 in the Gawler Ranges, but again K = 3 (Fig. 4), which also had a high ΔK value, appeared to be better supported by other analysis. The colonies from the Grey Range also showed some limited genetic differentiation from PCoA, distance trees and STRU CTU RE analysis (K = 2 and K = 6, supported from ΔK and L(K)).  These results were also supported by pairwise F ST values, which were low, but still significant (p < 0.001; Table 3).

First-generation putative migration
Putative migration here is defined as shared sequence similarities (based on genetic distance, allele frequency and Bayesian criterion; Piry et al. 2004) exhibited geographically, thus suggesting a permanent movement event from one site to another, rather than the more general definition of ecological migration, which relates to season and resource. Out of 71 individuals (46 in the Gawler Ranges and 25 in the Grey Range) 17 were identified as putative f 0 putative migrants (  (Smith et al. 2020a, b, c).

Key findings
This study aimed to examine contemporary movement between disjunct colonies of P. xanthopus with varying (1) Bar plots showing the major clusters for K = 2 and K = 3 (all 10/10 iterations, i.e. no minor clustering). K = 2 was most supported by Evanno's ΔK method, though K = 3 was better supported by other methods of examining population structure. (2) Bar plots showing K = 2 and K = 3 for the Gawler Dataset and (4) K = 2 and K = 6 for the Grey Range Datasetfrom structure analysis are also shown. Graphs of ΔK and L(K) over each value of K and bar plots of all clusters (K = 1-10) can be found in the Supplementary material levels of connectedness in both South Australia and Queensland. We found though the examination of population structure, kinship analysis and maximum likelihood analysis of putative migration that there has likely been recent contemporary movement. Individuals with kinship values greater than 0.0625 were common between colonies within the Gawler Ranges with several movements greater than 13 km, and despite an approximately 5 km gap of unsuitable habitat, related individuals were present from the two sampled locations in the Grey Range. Further to this, multiple putative f 0 migrations were identified within both the Gawler and Grey Ranges. From these results it is clear that P. xanthopus are more mobile within mountain ranges than previously assumed. The results from the Gawler ranges colonies in particular add weight to recently published results also showing several potential long distance migration events of P. xanthopus in the Flinders Ranges (Potter et al. 2020). This previous study primarily focused the genetic variation of colonies, but provided insight into potential movements between colonies that was more thoroughly examined here. Greater mobility of rock-wallabies also fits closer with metapopulation theory, where movement between semi-isolated demes and back into locally extinct or new sites helps maintain the genetic and ecological viability of the broader population (Hanski 1998). This new understanding is likely to affect future management of the species. Visual representation of relatedness estimates greater than 0.0625 generated though Identity by Descent (IBD) analysis. Coloured circles (nodes) show individuals of each population, relatedness lines (edges) are weighted by the strength of the relationship (not comparable between populations). Grouped node locations correspond to geographic locations (Fig. 1)

Population structure
The initial analysis of population structure across all samples (Primary Dataset) showed that each mountain range should be considered independent of the others when considering genetic monitoring within the species. These results are in agreement with the literature on P. xanthopus genetics and phylogeny which splits the South Australian and Queensland species into subspecies, and shows that separate mountain ranges/populations are genetically distinct (Eldridge 1997;Pope et al. 1996Pope et al. , 1998Potter et al. 2012Potter et al. , 2020. Populations of P. xanthopus were shown to have an order of magnitude greater pairwise F ST values between mountain ranges than within mountain ranges (Table 3), and all other methods employed for determining genetic differentiation between populations and individuals supported this result (Figs. 2, 3,  Fig. S4 and Tables S6-S10). Given the ΔK method has the propensity to lead to over identification of K = 2 (Cullingham et al. 2020;Janes et al. 2017), STRU CTU RE and other methods indicated that3 was best supported K value). From the initial structure analysis there was also evidence of some population substructuring, leading us to examine fine-scale structure in data subsets based on each of the populations. This showed that there was indeed some genetic structuring between colonies of each population, though not nearly as distinct as between mountain ranges (Figs. 3, 4). Fine scale structure is also supported by the recent analysis of microsatellite loci, which showed some structure within colonies within the Flinders Ranges (Potter et al. 2020).

Genetic diversity
Greater genetic diversity in populations is closely linked to a population's ability to withstand genetic pressures associated with small population size and to adapt to changing environmental conditions (Frankham 2005). Our results in rock-wallabies showed that the smaller, less geographically connected, populations in the Gawler and Grey Ranges have lower genetic diversity (H O and A R ) than those of the Flinders Ranges (Waukawoodna site- Table 2). This outcome is in concordance with assumptions that genetic diversity should be positively correlated with population size (Frankham 1996). Significance testing of F IS also revealed all colonies (with the exception of Alaric in the Grey Range) significantly deviate from zero, the null value, indicating either heterozygote deficiency (Yandinga, Organ Pipes, Waukawoodna) or heterozygote excess (Ray, Coolgundibie and Stone Dam). While the theory behind inbreeding leading to heterozygote deficiency is well established (Buri 1956), the processes leading to heterozygote excess are less clear. Though there are several potential explanations (referenced and discussed in Stevens et al. 2007), this case is likely due to the small population sizes. Binomial sampling error can cause differences in allele frequencies of male and female breeders, leading to heterozygote excess in their progeny (Luikart and Cornuet 1999;Robertson 1965;Waples 2015). This explanation of heterozygote excess in these rock-wallaby colonies is supported by the estimates of effective population size (N e ), which are substantially smaller in the corresponding colonies (Table 2).

Inter-colony relationships and movement
The first step employed here to examine how P. xanthopus move between colonies was assessing pairwise relatedness (r) between all individuals of a population. The analysis revealed relationships greater than the 0.065 (i.e. a common ancestor within 4 generations) threshold between all colonies within each population (excluding the Flinders Ranges), and one relationship of ~ 0.5 (indicating a full-sibling or parentprogeny relationship) between two colonies in the Gawler Ranges.. These relationships also indicate that there may be greater mobility between populations than previously recognised based on early genetic assessments (Pope et al. 1996).
While these results indicate recent movement between the colonies, inter-colony r values that are further apart Individuals identified as potential first generation migrants in Gene-Class2. Table shows the colony the individual was captured in (Sampling colony) and the likely colony the individual emigrated from. The distance between the source and original colony is listed in kilometres. The log value of the ratio of 'likelihood of home' over 'likelihood of all populations', the log value of the 'likelihood of home', and the log value of the greatest likelihood (corresponding to the Emigrated from colony) were also included. All probabilities of the log-likelihood ratio were equal to 0 To identify the likely coloniesof-origin, putative f 0 migrants were identified in Gene-Class2. The program identified 15 potential first generation migrants in the Gawler Ranges, and two in the Grey Range (Table 4). As might have been postulated from the analysis of population structure, movement between Organ Pipes and Yandinga constituted a large percentage of putative migrants. These colonies are separated by only 2.9 km of suitable habitat (Fig. 1). As P. xanthopus are known to move up to 1.5 km to water points (Sharp 2011), this regular exchange of individuals was expected. Less predictable were the putative migrants into and from Stone Dam, and those from the Yandinga/Organ Pipes area, found at Coolgundibie. Interestingly, no f 0 migrants were identified as having dispersed in the reverse direction, i.e. Coolgundibie to any other colony in the Gawler Ranges. Despite this exception, within the Gawler Ranges rock-wallabies appear to move readily to areas of connected habitat, even over relatively large distances.
Within the Grey Range population, only two migrants were detected, with both indicating the individual moved from Alaric to Ray. These movements are of particular relevance, both to the understanding of species population dynamics, and to future management of the species in Queensland. The area of the Grey Range that these two colonies reside in is at the very Southern end of P. x. celeris' distribution. The Alaric colony is located on the Canaway Fault, a line of connected rock-wallaby habitat/cliffs that run the North-South. The Ray colony, however, is approximately 8 km distant on fragmented rocky outcrops known as The Matrix. As previously mentioned, the shortest distance between suitable rock-wallaby habitat between the Canaway Fault and The Matrix is ~ 5 km of open, flat, farmland. Moreover, this dispersal route is now impeded by an exclusion fence (Fig. 1).

Management implications
Early assessments of the Gawler ranges had not found colonies of P. xanthopus at Coolgundibie (Lethbridge 2004a) or Stone Dam (Lethbridge et al. 2012;Lethbridge et al. 2010). In part, samples were collected from these colonies to assess whether theylikely represent recolonisation events from the other established colonies under threat abatement. The high kinship values between samples from these colonies and those of Yandinga and Organ Pipes suggest that movement reported here likely reflect recolonisation as a result of 25 years of goat and fox control (and some kangaroo management) and a major drought in the Gawler Ranges (Lethbridge et al. 2019). Integrated pest management (of feral rabbits Oryctolagus cuniculus, foxes, goats, cats Felis catus and weeds) may have driven this pulse of movement as a reduced number of predators, and also a shortage of resources in core P. xanthopus colonies, induced densitydependant dispersal behaviours. Continued recovery of rock-wallabies under these conditions likely depends on the threat abatement being widespread enough to facilitate further recolonisation events at sites that, without abatement, would be unsuitable.
For P. x. celeris, the rapid expansion of pest-exclusion fencing in the area (Smith et al. 2020c) potentially divides colonies that have previously relied on movement to maintain greater levels of genetic diversity, such as that of the Flinders Ranges (Table 2). In all cases, identified f 0 migrants (Table 4) were also those with higher inter-colony kinship values in the relatedness network (Fig. 5). The fence between the two colonies was completed in 2016, so either the rockwallabies were able to pass across the exclusion fence, or the rock-wallabies relocated colonies prior to the exclusion fences construction. The fences have proved highly effective at preventing the movement of other species (RAPAD and QFPI 2018), and aging the potential migrants based on tail-length data (Lethbridge 2004b) showed that dispersal pre-2016 was possible. It would be reasonable to assume that the migrants moved colonies pre-fence, and that the population in Queensland is now fragmented by exclusion fencing (Smith et al. 2020c). Indications that the rapid reduction in P. xanthopus distribution over the past century has already had negative genetic impacts on population viability which makes this assessment all-the-more troubling (Potter et al. 2020). This is particularly true of colonies, such as the Ray colony, that were already not part of connected and continuous rock-wallaby habitat. To allay the potential negative impacts, the genetic variation of isolated populations would have to be monitored into the future and mitigation strategies such as meta-population management be employed if/ when the populations appear to be experiencing genetic erosion. Meta-population management has been successfully employed for the maintenance of genetic variation issues caused by fencing in the past (Boast et al. 2018;Miller et al. 2015;Schroeder 2019).

Limitations
While most F IS values deviated significantly, they may not reflect the true value in the populations. Estimation of both F IS and N e assumes random mating and random sampling in the population; both assumptions may have been violated here. For P. xanthopus there is evidence of social structure, dominance behaviours and philopatry (Lapidge 2001;Potter et al. 2020;Sharp 2002) and territorial defence (or more specifically, trap bait defence) which may result in non-random sampling. Additionally, clear delimitations between sampling populations is needed to avoid Wahlund effects (De 1 3 Meeûs, 2018;Wahlund 1928;Waples 2015). As it appears colonies have an exchange of individuals (Fig. 5), colonies likely represent demes of a metapopulation, and this may have altered F IS estimates of colonies.
This study also lacked a proper 'control' site, which demonstrably functions as a healthy metapopulation, and replication within the separate populations. Understandably, even with sufficient time and resources, finding and sampling populations and colonies to remove this limitation is difficult in threatened species.

Future research
It is clear from the results above that for the effective conservation and recovery of P. xanthopus, the management of the species needs to be considered at a broader scale. The long term conservation of the species relies on the ability of individuals to immigrate into neighbouring colonies for the maintenance of genetic variation (Potter et al. 2020). Further to this, the recovery of the species relies on an increase in the species distribution as potentially suitable habitats become available as a result of broad scale management of threatening processes (Lethbridge et al. 2012;Lethbridge et al. 2019). Future research should seek to elucidate whether recolonised sites continue to be genetically supplemented from other colonies in the metapopulation. Additionally, as new sites arise, genetic assignment of colonising rock-wallabies should be made a priority to establish source populations. More specifically for P. x. celeris, continuing genetic monitoring should be implemented alongside long term studies of behaviour (and simulations of metapopulation movement and genetics) both to ensure genetic viability of the population is maintained and as a study of the long term effects of anthropogenic barriers on species genetics and behaviour (Smith et al. 2020a, b, c).
Molecular ecology tools can often be overlooked in favour of more traditional methods of assessing species. The above study clearly demonstrates the application of genetic ecology methods, specifically kinship analysis, to help inform management of a threatened species. By applying these more appropriate methods for a cryptic and disjunct species we were able to infer regular movement between colonies where previous studies failed to find movements or significantly underestimated their regularity. Studies of species that have had similar short comings should consider how genetic analysis could overcome these obstacles and better inform the species management.