- Research article
- Open Access
Population genetic structure and evolutionary history of Bale monkeys (Chlorocebus djamdjamensis) in the southern Ethiopian Highlands
BMC Evolutionary Biology volume 18, Article number: 106 (2018)
Species with a restricted geographic distribution, and highly specialized habitat and dietary requirements, are particularly vulnerable to extinction. The Bale monkey (Chlorocebus djamdjamensis) is a little-known arboreal, bamboo-specialist primate endemic to the southern Ethiopian Highlands. While most Bale monkeys inhabit montane forests dominated by bamboo, some occupy forest fragments where bamboo is much less abundant. We used mitochondrial DNA (mtDNA) sequences to analyse the genetic structure and evolutionary history of Bale monkeys covering the majority of their remaining distribution range. We analysed 119 faecal samples from their two main habitats, continuous forest (CF) and fragmented forests (FF), and sequenced 735 bp of the hypervariable region I (HVI) of the control region. We added 12 orthologous sequences from congeneric vervets (C. pygerythrus) and grivets (C. aethiops) as well as animals identified as hybrids, previously collected in southern Ethiopia.
We found strong genetic differentiation (with no shared mtDNA haplotypes) between Bale monkey populations from CF and FF. Phylogenetic analyses revealed two distinct and highly diverged clades: a Bale monkey clade containing only Bale monkeys from CF and a green monkey clade where Bale monkeys from FF cluster with grivets and vervets. Analyses of demographic history revealed that Bale monkey populations (CF and FF) have had stable population sizes over an extended period, but have all recently experienced population declines.
The pronounced genetic structure and deep mtDNA divergence between Bale monkey populations inhabiting CF and FF are likely to be the results of hybridization and introgression of the FF population with parapatric Chlorocebus species, in contrast to the CF population, which was most likely not impacted by hybridization. Hybridization in the FF population was probably enhanced by an alteration of the bamboo forest habitat towards a more open woodland habitat, which enabled the parapatric Chlorocebus species to invade the Bale monkey's range and introgress the FF population. We therefore propose that the CF and FF Bale monkey populations should be managed as separate units when developing conservation strategies for this threatened species.
The distribution and diversity of species are shaped by a combination of historical and contemporary factors. Currently, many species are affected by accelerated habitat destruction caused by both climate change and anthropogenic activity, the result being fragmentation, population decline and loss of genetic diversity [1,2,3,4,5,6,7,8]. The effects of habitat alteration are particularly detrimental to species with small geographic ranges and specialized niche requirements [2, 5, 9,10,11]. One such species severely affected by habitat fragmentation is the Bale monkey (Chlorocebus djamdjamensis) [12, 13]. This arboreal primate is endemic to the southern Ethiopian Highlands [14,15,16] and by far the most range-restricted of all green monkeys (genus Chlorocebus) [17, 18]. The taxonomy of green monkeys is disputed, but we here follow Groves  and accept the division of the genus into six species. In addition to the Bale monkey, Ethiopia harbours two other native, but not endemic Chlorocebus species, the vervet (C. pygerythrus) and the grivet (C. aethiops) [16, 19,20,21]. These two species are widely distributed, semi-terrestrial ecological generalists, inhabiting a variety of habitats and consuming a diverse diet of plant resources, invertebrates and small vertebrates [16, 22,23,24]. The Bale monkey, on the other hand, inhabits montane bamboo forests [14,15,16] where it feeds primarily on the young leaves and shoots of highland bamboo (Arundinaria alpina) . Despite differences in habitat and dietary requirements, interspecific gene flow with grivets and vervets has been suggested to occur in the contact zones that are found in the fragmented part of the Bale monkey's range [12, 26]. A phylogenetic study by Haus et al.  revealed incongruences between mtDNA lineages and phenotypes in African green monkeys and suggested the occurrence of introgression between Bale monkeys and grivets as well as between vervets and grivets in Ethiopia.
In modern times, conversion of the bamboo forest into agriculture and human settlement has resulted in population fragmentation in parts of the Bale monkey’s range. Although the species is locally abundant in the remaining continuous bamboo forests, e.g., Odobullu Forest [14, 15] (Fig. 1), populations found in forest fragments are generally small and declining and some have been extirpated in recent decades . The total remaining population size of Bale monkeys is estimated to be less than 10,000 individuals [Mekonnen, unpublished data] with a declining trend [14, 15]. The species is classified as Vulnerable by the IUCN . With the exception of the bamboo forests of Bale Mountains National Park (BMNP), most of the current Bale monkey range is located outside formally protected areas [14, 15] where the species is threatened by hunting and possibly by hybridization with grivets and vervets [12, 16, 20].
Bale monkeys are one of the least-studied African primates . Therefore, baseline data on their phylogenetic position, population genetic structure and evolutionary history are crucial for assessing the conservation status of the taxon and for designing and implementing effective management strategies [7, 27,28,29,30]. Hence, we aimed to investigate the phylogeography and genetic diversity of Bale monkeys using the hypervariable region I (HVI) of the mitochondrial (mtDNA) control region (CR). This marker is rapidly evolving in vertebrates  and thus suitable to studying events that took place during the Pliocene-Pleistocene period. Particularly for female philopatric mammals, mtDNA markers have been considered more suitable than nuclear DNA markers to describe phylogeographic processes, even though they only reflect the maternal history [32, 33]. MtDNA has been widely used to detect molecular signatures of demographic changes [34,35,36,37]. However, a single-locus study will not adequately reflect the entire evolutionary history of a species [38, 39]. With so many of the world’s animal taxa currently threatened, single-locus studies are, nevertheless, useful when designing science-based management regimes aimed at enhancing the prospects of survival for little-studied species (e.g., ).
In particular, the main aims of the study were to investigate the following three objectives. First, we reconstructed phylogenetic relationships and estimated divergence times among Bale monkey populations and other green monkeys in Ethiopia. Second, we investigated genetic structuring within and between Bale monkey populations inhabiting continuous forest (CF) and fragmented forests (FFs). Third, we examined if any differences could be detected in the demographic histories of Bale monkey populations.
Our study leads to enhanced understanding on how rare specialist species may be affected by habitat alterations and demonstrates that genetic data, even from a single marker, can provide information that will be vital for future conservation efforts.
Study area and sample collection
The geographic range of the Bale monkey has been estimated as approximately 12,500 km2 . Our study area covers the current species range in the southern Ethiopian Highlands, including both the CFs of the Bale Mountains  and the FFs of the Sidamo Highlands  (Fig. 1).
Chlorocebus djamdjamensis, C. aethiops, and C. pygerythrus were identified by phenotypic differences in their morphology, including coat colour, tail length and colour, facial hair (e.g., moustache) and whisker length [12, 16, 20]. Putative hybrids were identified by their intermediate coat colour, tail length, whisker length, and face colour and shape (Additional file 1). The presence of C. aethiops × C. pygerythrus hybrids with intermediate phenotypes at Arba Minch (Fig. 1) was described by Haus et al. .
Fresh faecal samples were noninvasively collected from May to December 2013 at three localities in CF and nine localities in FF (Fig. 1; Additional file 2). All of the FFs were small areas of less than 2 km2 embedded in a matrix of cultivated land and human settlements. The distance between the FFs varied between 3.5 km and 71.3 km through areas consisting of human settlements, grazing land, and cultivated land. Detailed information about sampling sites and samples are presented in Additional file 2.
Care was taken to avoid repeated sampling from the same individuals. In the FF habitat, where visibility was high, droppings were only collected from recognized individuals. In contrast, the CF habitat has areas with thick understory cover, where it was not always possible to sample only from identified individuals. Hence, we followed a particular group for up to one day and collected droppings within a short time interval whenever there was an opportunity [42, 43]. Since we collected only a few samples from each group – much less than the actual group sizes – the probability of sampling any one individual more than once was small. We cut the surface of each dropping and transferred it into a 50 ml plastic tube containing silica beads for preservation. In some cases, the faecal samples were dried under a tree (to avoid direct sunlight that can cause DNA degradation) to remove excess moisture before preservation. We also replaced the silica beads if additional desiccation was required. To avoid contamination, clean disposable gloves were used when handling samples during drying and exchange of silica beads. For each sampling event, geographic coordinates (using Garmin GPSMap 62s), habitat type and group size were recorded. Samples were transported to Addis Ababa University and stored at − 20 °C until they were shipped to the University of Oslo, Norway for DNA extraction and further processing.
We also included 12 faecal samples of grivets (8), vervets (2) and putative grivet x vervet hybrids (2) previously collected by Haus et al.  from nine localities in southern Ethiopia (Fig. 1; Additional file 2). These samples were kept for at least 24 h in ethanol (> 90%) and then stored on silica beads after drying . Further details about the collection of these samples are outlined in Haus et al. .
Permission to conduct this research was granted by the Ethiopian Wildlife Conservation Authority in compliance with the Convention on International Trade in Endangered Species of Wild Fauna and Flora (CITES). Faecal samples were collected non-invasively without harming or disturbing the animals. This study meets all animal care policies and adheres to the legal requirements of Ethiopia, Norway, and Germany. It also complied with the ethical and legal requirements of the American Society of Primatologists Principles for the Ethical Treatment of Primates.
We extracted DNA from faecal samples following the protocol described in Atickem et al. . A thin slice (≤ 0.01 g) was cut from the surface of each sample using a clean razor blade and transferred to an Eppendorf tube containing 300 μl lysis buffer (500 mM Tris, 10 nM NaCl, 50 mM EDTA). After 30 min incubation at 56 °C and 1 min centrifugation, 100 μl of the lysate was transferred to a tube containing 95 μl isopropanol for DNA precipitation and 20 μl of Dynabeads® MyOne™ SILANE (Invitrogen Dynal AS Oslo Norway) for DNA binding. The tubes were then left for 2 min on a magnetic device before the supernatant was discarded. The DNA was washed twice with 200 μl 70% ethanol and finally eluted in 100 μl mqH2O preheated to 80 °C. We included one negative control per eight sample extractions.
DNA extraction from faecal samples collected by Haus et al.  was conducted with the QIAamp DNA Stool Mini Kit (Qiagen, Hilden, Germany) following standard protocols with only minor modifications . All DNA extracts were stored in 50 μl aliquots at − 20 °C until further processing. DNA concentrations were measured on a NanoDrop ND-1000 spectrophotometer (Thermo Fisher Scientific, Waltham, USA) or Qubit 2.0 (Thermo Fisher Scientific).
We amplified an approximately 800 bp long fragment of the HVI region from 131 samples. We conducted PCR reactions in a total volume of 30 μl containing a final concentration of 0.33 μM of each of the genus-specific primers 5’-AAATGAACTTGCCCTTGTAG-3′ and 5’-GGTGTTGCGTGCAGACC-3′, 3 mM MgCl2, 0166 mM dNTPs, 1× buffer, 1 U Biotherm Taq DNA polymerase (Genecraft, Cologne, Germany) and 100 ng DNA. The cycling conditions consisted of a pre-denaturation step at 94 °C for 2 min, followed by 40–50 cycles, each with denaturation at 94 °C for 1 min, annealing at 54 °C for 1 min, and extension at 72 °C for 1 min. At the end, a final extension step at 72 °C for 5 min was added. We checked PCR performance on 1% agarose gels. PCR products were excised from the gel, cleaned with the QIAquick Gel Extraction Kit (Qiagen, Hilden, Germany) and Sanger-sequenced in both directions on an ABI 3130xl DNA sequencer (Applied Biosystems, Foster City, USA) using the BigDye Cycle Sequencing Kit and the amplification primers. Sequence electropherograms were checked by eye with 4Peaks 1.8 (www.nucleobytes.com) and sequences were assembled and manually edited in SeaView 4.4.0 . Sequences were deposited in GenBank and are available under the accession numbers MG786940 - MG787070.
To avoid cross-sample contamination in the laboratory, all working steps (DNA extraction, PCR setup, PCR amplification, gel electrophoresis, PCR product purification, and sequencing) were conducted in separate and therefore dedicated laboratories under Captair Bio PCR cabinets (Erlab, Val de Reuil, France). Benches were cleaned with 10% bleach and gloves were regularly changed. Further, PCR controls (without template DNA) were routinely conducted and procedures were repeated for 10% of randomly selected samples. To minimize the risk of amplifying nuclear mitochondrial-like sequences (numts), we designed genus-specific primers on the basis of published mtDNA genomes from Chlorocebus . We tested these primers, using the lab methods mentioned above, in ten Chlorocebus individuals for which we recently generated mtDNA genomes . The obtained sequences were identical to their mtDNA genome orthologs, suggesting that the primers amplify solely mtDNA and no numts.
Phylogenetic reconstruction and divergence time estimation
For phylogenetic tree reconstructions, we added an orthologous sequence from Chlorocebus sabaeus (EF597503.1) to our dataset as an outgroup. Sequences were aligned with MUSCLE 3.8.31 , implemented in MEGA 7.0.14  and inspected by eye in BIOEDIT 7.2.5 . The best-fit nucleotide substitution model (HKY)  was selected using the Bayesian Information Criterion (BIC)  as implemented in jModeltest 2.1.6 . We constructed phylogenetic trees using both maximum-likelihood (ML) and Bayesian methods. A ML tree was constructed in MEGA with the nearest Neighbor-Interchange by bootstrapping 10,000 replicates. To reconstruct a Bayesian phylogenetic tree and to estimate divergence times, we applied the BEAST package 2.4.4 [53, 54]. Since no reliable fossil-based calibration points are available, divergence ages were calibrated based on the mtDNA split between C. sabaeus and all other Chlorocebus spp. using a normal distribution with a mean of 3.50 Mya and a 95% highest posterior density (HPD) of 3.10–3.90 Mya . We implemented the HKY model of nucleotide substitution with a relaxed uncorrelated lognormal clock model and a Yule model as tree priors. We conducted two Markov Chain Monte Carlo (MCMC) runs, each with 10 million generations, with trees sampled every 10,000 generations. Tracer 1.6 was used to investigate performance with a 10% burn-in and to verify that the effective sample size (ESS) was greater than 200. LogCombiner 2.4.4 was used to combine independent runs and TreeAnnotator 2.4.4 was applied to generate a consensus tree using maximum clade credibility with median node heights. We visualized and summarized the tree using the FigTree 1.4.2 drawing tool. We defined all clades with both bootstrap (BS) and posterior probability (PP) support of > 90% and > 0.90, respectively as significantly monophyletic.
To further trace phylogenetic relationships among haplotypes from all Bale monkeys and 12 other green monkeys, we constructed a TCS network (based on the method of Templeton et al.  that is particularly suitable to infering population level genealogies ) using the software PopART 1.7 .
Genetic diversity and population genetic structure
We estimated genetic diversity for each Bale monkey locality, CF, FF and overall populations as the number of haplotypes (a unique base sequence found in one or more individuals), haplotype diversity, nucleotide diversity and number of polymorphic sites  using Arlequin 188.8.131.52 . When the sampling sites were merged into CF and FF, the number of individuals was n = 34 and n = 85, respectively. For the purpose of comparison, we also included 12 sequences from other green monkeys.
We calculated genetic differentiation among local Bale monkey populations as pairwise fixation indices (FST) in Arlequin. We ran 10,000 permutations to assess if the population pairs were significantly (0.05% significance level) more differentiated than what would have been expected if haplotypes were randomly distributed among them. Theoretically, FST values range from 0 (no genetic differentiation) to 1 (complete genetic differentiation). We applied a Mantel’s test  to assess if the correlation between pairwise genetic (FST) and geographic distances (km) among all sampling sites were higher than what would be expected for a randomly reproducing population. The geographic distances were estimated using Geospatial Modeling Environment and ArcGIS 10.3 following Mekonnen et al.  and the Mantle’s test was performed in IBDWS 3.15  with 1000 permutations and a 95% confidence interval (CI). We analysed population genetic structure and differentiation within and between Bale monkey populations using Analysis of Molecular Variance (AMOVA) as implemented in Arlequin. Variance components within and among populations were calculated with 10,000 random permutations. In addition, we calculated pairwise genetic distances between populations and/or taxa using a Kimura-two-parameter (K2P) model as implemented in MEGA with 10,000 replicates.
Population demographic history
We tested for molecular signatures of demographic changes (sudden fluctuations in population size) in the evolutionary history of the Bale monkeys (CF, FF and overall) by running three widely used tests (e.g., [34, 62, 63]). First, we applied neutrality tests using Fu’s FS  and Tajima’s D  in Arlequin with 10,000 permutations. Second, we examined mismatch distribution of pairwise differences between sequences as implemented in Arlequin and DnaSP 5.10.1  with 10,000 bootstrap replicates. The statistical significance was determined by testing the goodness-of-fit between the observed and expected mismatch distributions, using the raggedness index (r)  and the sum of squared differences (SSD) before (θo) and after expansion (θ1) [68, 69]. Studies have demonstrated that the shape of the mismatch distribution generally exhibits multimodal and ragged distributions for stationary and non-expanding populations, whereas unimodal or smooth distributions indicate that populations have experienced historical demographic expansions or bottlenecks [68, 70]. Third, the demographic history of Bale monkey populations was inferred to assess effective population size changes using the Bayesian Skyline Plot (BSP) method  as implemented in BEAST. The BSP model assumes a single panmictic population and violation of this assumption can result in misleading demographic inferences [72, 73]. Although BSP assumes a single species or monophyletic group in analyses of demographic history, similar analyses have been carried out when modelling hybridization at population peripheries [74, 75]. Thus, we generated BSPs for genetically homogenous geographic populations as inferred by AMOVA (e.g., [34, 74, 75]). As substitution models, we applied HKY for the CF population and HKY + I for the FF population as they were chosen as best-fit models by jModeltest. The analyses were carried out using a relaxed uncorrelated lognormal clock with a coalescent Bayesian Skyline priori and a random starting tree. Time to the most recent common ancestor (MRCA) for each population was set to analyse their corresponding BSP using normal distribution. Two independent analyses were run for a total of 30 million MCMC generations sampling every 3000 generations with 10% of the samples as burn-in. The results of each run were checked to ensure convergence and stationarity using Tracer. Runs, where ESS values were less than 200 for all parameters, were discarded.
Phylogeny and estimation of divergence time
The final alignment had a length of 735 bp and contained 132 sequences, which were derived from samples of 119 Bale monkeys, eight grivets, two vervets, two individuals identified as grivet x vervet hybrids and one C. sabaeus sequence as an outgroup. Numts are highly unlikely to be present in our dataset, as we (1) used only faecal material in which nuclear DNA is largely degraded , (2) the HVI region was amplified with genus- and mtDNA-specific primers, and (3) no multiple peaks were obtained by direct sequencing of PCR products. We found 201 polymorphic sites, of which 168 were parsimony informative, and 33 were singletons. The alignment comprised of 26 haplotypes, of which 16 (H1-H16) were derived from phenotypical Bale monkeys, six (H17-H22) from phenotypical grivets, two (H23-H24) from phenotypical vervets, and two (H25-H26) from phenotypical grivet x vervet hybrids (Additional file 3).
The topology of our phylogenetic tree is similar to that of Haus et al.  and suggests two major clades for Ethiopian green monkeys (Fig. 2). One clade comprises all Bale monkey haplotypes from CF and represents a sister lineage to a vervet haplotype (H23) from Sof Omar, whereas the second clade contains all haplotypes from FF Bale monkeys as well as from vervets, grivets and their putative hybrids. Within the first clade, the CF Bale monkeys form a monophyletic group, which corresponds to clade C5 of Haus et al. , whereas in the second clade the FF Bale monkeys form a subclade which also contains haplotypes of C. pygerythrus and of pygerythrus/aethiops hybrids and corresponds to clade C2 of Haus et al. . The FF Bale monkey subclade forms a sister clade to several C. aethiops and pygerythrus/aethiops hybrid lineages. The vervet haplotype (H23) from Sof Omar represents clade C6 of Haus et al. . We will hereafter refer to the CF clades as Bale monkey clade and the FF clade as green monkey clade.
We estimated the divergence ages between the green monkey and Bale monkey clades at 2.79 (2.21–3.71) Mya, and the split of the Bale monkey clade from its sister lineage, H23 from Sof Omar, at 2.16 (1.41–2.3.21) Mya (Fig. 2). These divergence ages are similar to those based on complete mtDNA genomes by Dolotovskaya et al. . The age of the MRCA of the clade containing all of the haplotypes from FF Bale monkeys was estimated at 1.09 (0.61–1.81) Mya and that of the Bale monkey clade at 0.53 (0.25–0.93) Mya.
The two distinct clusters of CF and FF Bale monkey haplotypes also appeared in our TCS network (Fig. 3), although the pattern is more obscure here due to the location of several grivet, vervet and hybrid haplotypes between and within the two Bale monkey clusters.
Genetic diversity and population differentiation
Among the 16 Bale monkey haplotypes identified, only four were shared by two or more localities within the FF population, while the remaining 12 (75%) haplotypes were found only at one locality (Table 1; Additional file 3). H16 was the most frequent haplotype found in 31 of the Bale monkey samples (26.1%), while H10 and H12 were the rarest and found only in one individual each (Table 1). The genetic diversity parameters in terms of number of haplotypes (h), haplotype diversity (Hd), nucleotide diversity (π) and number of polymorphic sites (p) for each locality, the CF, FF and the overall Bale monkey populations are presented in Table 1. The highest haplotype diversity (0.778) was calculated for Kulla (FF) with four haplotypes, followed by Gerbicho (FF) and Shedem (CF). We observed similar levels of haplotype diversity for the CF (0.804) and FF (0.768) Bale monkey populations. Five of the nine FF localities and one of the three CF localities exhibited only one haplotype (Table 1). Overall, we observed higher nucleotide diversity in CF (0.0359) than in FF (0.0156).
We found significant genetic differentiation (pairwise FST) among most sampling localities of Bale monkeys, except between a few of the FF sites (p > 0.05, Additional file 4). The high FST values observed between some population pairs are explained by the absence of shared haplotypes. The AMOVA results suggested that as much as 87% of the total variability was explained by differentiation between the CF and FF populations (Table 2). The differentiation among sampling localities within populations explained 7.9%, and variability within locality explained 5.1% of the variation (Table 2). Further, we found a significant correlation between genetic and geographic distances (km) among all sampling localities of Bale monkeys (Mantel r = 0.66; p = 0.002), suggesting that the genetic structure of the Bale monkey follows a pattern of IBD. When testing for IBD among the FF sampling sites alone, the result was not significant (Mantel r = 0.342; p = 0.06). The genetic distance between CF and FF populations was estimated to be 14.1%, which is higher than the distance between CF and grivets (13.4%) and FF and grivets (9.8%).
Demographic history of Bale monkeys
The demographic history was analysed for the overall Bale monkey population as well as for the CF and FF populations separately. The CF population showed non-significant positive values for Fu’s FS and Tajima’s D (Table 3) indicating a stable demographic history. This result was corroborated by the highly ragged and multimodal mismatch distribution patterns with sharp peaks (Fig. 4a). The FF population showed non-significant positive values for Fu’s FS suggesting a stable demographic history. However, a small negative value for Tajima’s D suggested population expansion, though this result was not statistically significant. The mismatch distribution observed for the FF population was nearly multimodal, suggesting that the population has not undergone recent population expansion (Fig. 4b). Finally, the overall Bale monkey population showed non-significant positive values for both Fu’s FS and Tajima’s D (Table 3), again characteristic of a stable demographic history with stable population size. In addition, the mismatch distribution model showed multimodal and moderately ragged distribution patterns, suggesting demographic stability. In sum, the mismatch and neutrality analyses suggested that the CF, FF and overall Bale monkey populations have had stable population sizes and have not undergone recent population expansions. Likewise, BSPs revealed that the CF and FF Bale monkey populations generally showed prolonged demographic stability before they started to decline around 25,000 years ago (Figs. 4c and d).
Our genetic analyses (TCS network, phylogenetic trees and AMOVA) suggest a division of Bale monkeys into two distinct clusters corresponding to the geographic structuring between CF (Bale Mountains) and FF (Sidamo Highlands). No mtDNA haplotypes are shared between these clusters (Fig. 1). Notably, the haplotypes of the FF Bale monkeys clustered with grivet and vervet haplotypes rather than with those from their conspecifics in CF.
Phylogeny and divergence time
In general, our phylogeny and divergence ages are consistent with those based on complete cytochrome b sequences  or complete mtDNA genomes . Similar to previous studies, we found a lack of taxonomic clustering among Ethiopian Chlorocebus monkeys, strengthening the notion that mtDNA sequence analyses may not be suitable for taxonomic delimitation in Chlorocebus. In contrast to previous studies, which included just one specimen per taxon, our results demonstrate that the poly- and paraphyletic relationships remain among Ethiopian Chlorocebus monkeys even when a larger number of specimens are included. Interestingly, our results show that Bale monkeys living in their original undisturbed habitat (CF) form a monophyletic group suggesting no indication of hybridization, whereas the population in the fragmented and disturbed habitat (FF) clustered with vervets and grivets suggesting the FF population most likely represents an introgressed deme.
Hybridization across species boundaries is not uncommon when closely related taxa meet in contact zones [26, 74, 77, 78]. Hybridization is also not unusual between Chlorocebus species. Indeed, it was already suggested to occur by Haus et al.  and recently confirmed in a whole genome study . However, no Bale monkeys were included in the latter study. Nevertheless, observations on phenotypes suggest interspecific gene flow in some localities of FF Bale monkeys. In particular, putative phenotypic Bale monkey × grivet hybrids were recorded  and one Bale monkey × vervet hybrid was observed at Kokosa with intermediate coat colour, tail length, and whisker length [J.-M. Lernould, personal communication, A. Mekonnen, personal observation] (Additional file 1). The majority of phenotypes observed in FF suggest that this population is most likely a relict C. djamdjamensis population, which was introgressed by vervet and grivet monkeys. The FF populations may have captured their mtDNA haplotypes from grivets and vervets via female-mediated gene flow (e.g., [80, 81]), while retaining most of the phenotypic features and ecological behaviours (e.g., bamboo niche – when available – folivory and arboreality) of the typical Bale monkey [82,83,84]. However, slight differences between the CF and FF Bale monkeys in morphology  (Additional file 1), behavioural ecology [13, 83, 84] and gut microbiota  further support the hypothesis that gene flow has already altered the gene pool of the FF population, making these monkeys ecologically flexible and more similar to other Chlorocebus species [13, 83, 84]. Here, whole genome analyses will certainly help to solve the question of adaptation by hybridization.
We did not detect any haplotypes shared between CF and FF Bale monkey populations (Figs. 2 and 3) indicating that gene flow between the demes is not common. The CF and FF sampling sites are separated by a distance of about 100 km. Although sampling for the current study provides very good coverage of the distribution range, some Bale monkey sites are known to exist in the area between the CF and FF sites sampled. It is thus possible that intermediate haplotypes can be found here and future sampling from this area would contribute to an improved view of historic and contemporary gene flow in these primates.
If the FF deme is indeed an introgressed relict population of Bale monkeys, it is reasonable to ask why hybridization has occurred here but not in the CF deme? A possible explanation could be that the habitat in the western part of the Bale monkey’s range, i.e. in FF, changed from the original bamboo dominated forest into a more open woodland and fragmented habitat [12, 15, 16], thus making it more suitable for the generalist vervet and grivet monkeys. Whether the habitat change was a consequence of natural climate change or the result of anthropogenic habitat alteration cannot be resolved at present. However, we suspect that both factors played a role and that human impact has probably been most influential over the last few centuries.
Population genetic structure
Although Bale monkeys have been extirpated in some FF localities in recent decades  and several FF localities lack genetic diversity, overall we found nearly similar levels of haplotype diversity in CF and FF populations (Table 1). However, the pattern of how haplotypes were distributed among sampling sites differed remarkably within the CF and FF populations (Fig. 3; Table 1). Within CF, none of the haplotypes were shared among sites, whereas eight out of nine FF sites (except Gerbicho) shared one or more haplotypes with other FF sites (Table 1). When several haplotypes were found within a FF sampling site, they were not necessarily closely related (e.g., H7 and H13, Table 1; Fig. 3), a pattern which is suggestive of genetic drift (random changes in haplotype frequency from generation to generation) . The haploid nature of mtDNA and the fact that it is only maternally inherited leads to an effective population size that is four times smaller compared to autosomal nuclear DNA. The influences of genetic drift and population bottlenecks will thus be more clearly expressed, with large inter-population differentiation, when working with mtDNA . Like many cercopithecines, including the other Chlorocebus spp. [23, 87], Bale monkeys are believed to exhibit male dispersal and female philopatry. It is thus possible that nuclear markers would display less differentiation among sampling sites due to male gene flow. Presently it is, however, unlikely that Bale monkey males move between isolated sites in the FF due to human disturbance [12, 15]. A number of studies have shown that habitat fragmentation may affect genetic structure by limiting movement between demes, and hence gene flow [10, 11, 88, 89]. The Bale monkey’s arboreal lifestyle and specialized niche [25, 84] limit its dispersal ability and thus make it particularly prone to genetic isolation due to extensive gaps in suitable habitat. The habitat gaps may be caused by human disturbance, climate change, and the landscape features of the southern Ethiopian Highlands (e.g., deep gorges and alpine areas above the tree line) .
Like for other African green monkeys , we found no genetic evidence for historical population expansion for the Bale monkey populations (Table 3). The recent population decline, as revealed by BSP, might be explained by climate change during and following the Last Glacial Maximum (LGM, 23,000–18,000 years before present), a period characterized by cool and wet climatic conditions in the southern Ethiopian Highlands . Since the Bale monkey populations are confined to a narrow geographic range with restricted suitable habitat (bamboo forest) , a reduction of suitable habitat and thus a reduction of the species’ range is to be expected. Currently, the FF populations are restricted to small isolated forest fragments mainly resulting from anthropogenic habitat modification [12, 15], which probably had an additional negative impact on Bale monkey population size in the last few centuries. We do note, however, that our BSP-based inferences into the demographic history of Bale monkeys should be interpreted with caution because of the confounding effect of the strong population structure that can lead to false inferences of population decline [72, 93, 94]. Further, we used a single mtDNA locus which is not likely to reflect the complete demographic history of the species (cf., ).
Implications for conservation
Bale monkeys are currently at high risk of extinction because of habitat alteration, hunting and possibly hybridization [12, 15, 41]. Science-based management strategies may thus be the only means to ensure the species’ long-term persistence. Studies of population genetic structuring of mtDNA have been applied to help identify management units appropriate for the conservation of endangered species [27,28,29, 40, 96]. The results of our study suggest two isolated Bale monkey populations, of which one (FF) most likely consists of hybrids with other Chlorocebus species. We therefore propose that two separate management units should be defined when designing strategies for the long-term conservation of Bale monkeys to preserve their unique genetic diversity and evolutionary potential.
Because the CF population represents what is believed to be the typical Bale monkey population – and is not sympatric with any other Chlorocebus species – we propose that this population warrants special conservation attention. We therefore recommend improved protection of continuous bamboo forest habitats by minimizing logging of bamboo for local consumption and commercial purposes. The FF population of the Sidamo Highlands is rapidly shrinking due to increasing anthropogenic impacts [12, 15, 41]. We therefore suggest connecting forest fragments to increase gene flow between isolated populations and prevent loss of genetic diversity, thereby promoting the long-term survival of these populations [97, 98]. Further, hybridization/introgression between Bale monkeys of the FF populations and the widely distributed vervets and grivets may have consequences for conservation. Provisionally, the FF population should be managed separately from parapatric vervets and grivets, at least until hybridization among them is confirmed. The impacts of hybridization on the conservation strategies for rare and threatened taxa can be complex and controversial [99, 100]. Hybridization may help to rescue small populations through increasing genetic variation by replacing parental genes with adaptive hybrid genes and consequently increasing the potential for adaptation in a changing environment and sometimes the formation of new species or subspecies [74, 101,102,103,104]. On the other hand, hybridization may lead to the extinction of rare and endangered species through genetic swamping of native populations [105,106,107]. When hybridization occurs in a large geographic range, it can cause a decrease in the total population size of native and range-restricted species through the loss of historically original populations. Conversely, hybridization can result in range expansion for non-endangered and widely adapted species . Such events could negatively impact the total population size and conservation status of the rare and specialist Bale monkey given that is surrounded by two widely distributed, generalist sister species in southern Ethiopia.
In our study, we demonstrated strong genetic differentiation between Bale monkeys from the Bale Mountains (CF) and the Sidamo Highlands (FF). Populations from the two habitat types differ not only in mtDNA but also in morphology  (Additional file 1), ecology and behaviour [13, 83, 84] as well as in gut microbiota . The differentiation was most likely initiated by habitat alteration due to past climate change. Bamboo forests, suitable for Bale monkeys, were replaced by a more open woodland habitat in the western part of the species' range, making introgression by parapatric Chlorocebus species possible. This alteration of the bamboo forest was later intensified and accelerated by human activities. As a consequence of genetic differentiation, we propose that the CF and FF Bale monkey populations should be managed as separate units. Overall, the results of this study increase our general understanding of how habitat fragmentation, hybridization and geographic isolation together have shaped the genetic structure of a rare, range-restricted and specialist primate. Future research focusing on bi-parentally and paternally inherited genetic markers, as well as morphological and ecological variability within the species, will be needed to further increase our understanding of the evolutionary history of this unusual species.
Analysis of Molecular Variance
Bayesian Information Criterion
Bayesian Skyline Plot
Convention on International Trade in Endangered Species of Wild Fauna and Flora
Effective sample size
Hypervariable region I
International Union for Conservation of Nature
Last Glacial Maximum
Markov Chain Monte Carlo
Most recent common ancestor
Million years ago
Sum of squared differences
Haddad NM, Brudvig LA, Clobert J, Davies KF, Gonzalez A, Holt RD, Lovejoy TE, Sexton JO, Austin MP, Collins CD, et al. Habitat fragmentation and its lasting impact on Earth’s ecosystems. Sci Adv. 2015;1:e1500052.
Dixo M, Metzger JP, Morgante JS, Zamudio KR. Habitat fragmentation reduces genetic diversity and connectivity among toad populations in the Brazilian Atlantic coastal Forest. Biol Conserv. 2009;142:1560–9.
Goossens B, Sharma R, Othman N, Kun-Rodrigues C, Sakong R, Ancrenaz M, Ambu LN, Jue NK, O'Neill RJ, Bruford MW, Chikhi L. Habitat fragmentation and genetic diversity in natural populations of the Bornean elephant: implications for conservation. Biol Conserv. 2016;196:80–92.
Estrada A, Garber PA, Rylands AB, Roos C, Fernandez-Duque E, Di Fiore A, Nekaris KA-I, Nijman V, Heymann EW, Lambert JE, et al. Impending extinction crisis of the world’s primates: why primates matter. Sci Adv. 2017;3:e1600946.
Pauls SU, Nowak C, Bálint M, Pfenninger M. The impact of global climate change on genetic diversity within populations and species. Mol Ecol. 2013;22:925–46.
Brook BW, Sodhi NS, Ng PK. Catastrophic extinctions follow deforestation in Singapore. Nature. 2003;424:420–6.
Miranda EA, Ferreira KM, Carvalho AT, Martins CF, Fernandes CR, Del Lama MA. Pleistocene climate changes shaped the population structure of Partamona seridoensis (Apidae, Meliponini), an endemic stingless bee from the Neotropical dry forest. PLoS One. 2017;12:e0175725.
Mairal M, Sanmartín I, Herrero A, Pokorny L, Vargas P, Aldasoro JJ, Alarcón M. Geographic barriers and Pleistocene climate change shaped patterns of genetic variation in the eastern Afromontane biodiversity hotspot. Sci Rep. 2017;7:45749.
Colles A, Liow LH, Prinzing A. Are specialists at risk under environmental change? Neoecological, paleoecological and phylogenetic approaches. Ecol Lett. 2009;12:849–63.
Groot AT, Classen A, Inglis O, Blanco C, López J, Téran Vargas A, Schal C, Heckel DG, Schöfl G. Genetic differentiation across North America in the generalist moth Heliothis virescens and the specialist H. subflexa. Mol Ecol. 2011;20:2676–92.
Fietz J, Tomiuk J, Loeschcke V, Weis-Dootz T, Segelbacher G. Genetic consequences of forest fragmentation for a highly specialized arboreal mammal - the edible dormouse. PLoS One. 2014;9:e88092.
Mekonnen A, Bekele A, Fashing PJ, Lernould J-M, Atickem A, Stenseth NC. Newly discovered Bale monkey populations in forest fragments in southern Ethiopia: evidence of crop raiding, hybridization with grivets, and other conservation threats. Am J Primatol. 2012;74:423–32.
Mekonnen A, Fashing PJ, Bekele A, Hernandez-Aguilar RA, Rueness EK, Nguyen N, Stenseth NC. Impacts of habitat loss and fragmentation on the activity budget, ranging ecology and habitat use of Bale monkeys (Chlorocebus djamdjamensis) in the southern Ethiopian Highlands. Am J Primatol. 2017;79:e22644.
Mekonnen A, Bekele A, Hemson G, Teshome E, Atickem A. Population size and habitat preference of the Vulnerable Bale monkey Chlorocebus djamdjamensis in Odobullu Forest and its distribution across the Bale Mountains, Ethiopia. Oryx. 2010;44:558–63.
Butynski TM, Gippoliti S, Kingdon J, De Jong Y. Chlorocebus djamdjamensis. The IUCN Red List of Threatened Species 2008: e.T4240A10699069. https://0-doi-org.brum.beds.ac.uk/10.2305/IUCN.UK.2008.RLTS.T4240A10699069.en. 2008. Accessed 02 Nov 2017.
Kingdon J. The Kingdon field guide to African mammals. 2nd ed. London: Bloomsbury Publishing; 2015.
Zinner D, Fickenscher GH, Roos C, Anandam MV, Bennett EL, Davenport TR, Davies NJ, Detwiler KM, Engelhardt A, Eudey AA. Family Cercopithecidae (Old World monkeys). In: Mittermeier RA, Wilson DE, Rylands AB, editors. Handbook of the Mammals of the World: Primates. Barcelona: Lynx Edicions; 2013.
Groves CP. Primate taxonomy. Washington: Smithsonian Institution; 2001.
Groves C, Primates O. In: Wilson DE, Reeder DM, editors. Mammal species of the world: a taxonomic and geographic reference. 3rd ed. Baltimore, MD: Johns Hopkins University Press; 2005. p. 111–84.
Haus T, Akom E, Agwanda B, Hofreiter M, Roos C, Zinner D. Mitochondrial diversity and distribution of African green monkeys (Chlorocebus gray, 1870). Am J Primatol. 2013;75:350–60.
Anandam MV, Bennett EL, Davenport TRB, Davies NJ, Detwiler KM, Engelhardt A, Eudey AA, Gadsby EL, Groves CP, Healy A, et al. Family Cercopithecidae (Old World monkeys) – species accounts of Cercopithecidae. In: Mittermeier RA, Rylands AB, Wilson DE, editors. Handbook of the mammals of the world Vol 3 Primates. Barcelona: Lynx Edicions; 2013. p. 628–753.
Isbell LA, Pruetz JD, Young TP. Movements of vervets (Cercopithecus aethiops) and patas monkeys (Erythrocebus patas) as estimators of food resource size, density, and distribution. Behav Ecol Sociobiol. 1998;42:123–33.
Jaffe KE, Isbell LA. The guenons: polyspecific associations in socioecological perspective. In: Campbell CJ, Fuentes AF, MacKinnon KC, Bearder SK, Stumpf RM, editors. Primates in perspective. 2nd ed. New York: Oxford University Press; 2011. p. 277–300.
Tournier E, Tournier V, van de Waal E, Barrett A, Brown L, Bshary R. Differences in diet between six neighbouring groups of vervet monkeys. Ethology. 2014;120:471–82.
Mekonnen A, Bekele A, Fashing PJ, Hemson G, Atickem A. Diet, activity patterns, and ranging ecology of the Bale monkey (Chlorocebus djamdjamensis) in Odobullu Forest, Ethiopia. Int J Primatol. 2010;31:339–62.
Detwiler KM, Burrell AS, Jolly CJ. Conservation implications of hybridization in African cercopithecine monkeys. Int J Primatol. 2005;26:661–84.
Moritz C. Defining Evolutionarily-Significant-Units for conservation. Trends Ecol Evol. 1994;9:373–5.
Palsbøll PJ, Berube M, Allendorf FW. Identification of management units using population genetic data. Trends Ecol Evol. 2007;22:11–6.
Funk WC, McKay JK, Hohenlohe PA, Allendorf FW. Harnessing genomics for delineating conservation units. Trends Ecol Evol. 2012;27:489–96.
Allendorf FW, Luikart G, Aitken SN. Conservation and the genetics of populations. 2nd edn. Chichester: John Wiley and Sons; 2013.
Broughton RE, Reneau PC. Spatial covariation of mutation and nonsynonymous substitution rates in vertebrate mitochondrial genomes. Mol Biol Evol. 2006;23:1516–24.
Avise JC. Phylogeography: retrospect and prospect. J Biogeogr. 2009;36:3–15.
Lowe A, Harris S, Ashton P. Ecological genetics: design, analysis, and application. Oxford: Blackwell Publishing; 2004.
Fratini S, Ragionieri L, Deli T, Harrer A, Marino IAM, Cannicci S, Zane L, Schubart CD. Unravelling population genetic structure with mitochondrial DNA in a notional panmictic coastal crab species: sample size makes the difference. BMC Evol Biol. 2016;16:150.
Rivera DS, Vianna JA, Ebensperger LA, Eduardo Palma R. Phylogeography and demographic history of the Andean degu, Octodontomys gliroides (Rodentia: Octodontidae). Zool J Linnean Soc. 2016;178:410–30.
González-Wevar CA, Hüne M, Cañete JI, Mansilla A, Nakano T, Poulin E. Towards a model of postglacial biogeography in shallow marine species along the Patagonian Province: lessons from the limpet Nacella magellanica (Gmelin, 1791). BMC Evol Biol. 2012;12:139.
Yang M, Yang Y, Cui D, Fickenscher G, Zinner D, Roos C, Brameier M. Population genetic structure of Guizhou snub-nosed monkeys (Rhinopithecus brelichi) as inferred from mitochondrial control region sequences, and comparison with R. roxellana and R. bieti. Am J Phys Anthropol. 2012;147:1–10.
Moritz C, Cicero C. DNA barcoding: promise and pitfalls. PLoS Biol. 2004;2:e354.
Heled J, Drummond AJ. Bayesian inference of population size history from multiple loci. BMC Evol Biol. 2008;8
Karamanlidis AA, Gaughran S, Aguilar A, Dendrinos P, Huber D, Pires R, Schultz J, Skrbinšek T, Amato G. Shaping species conservation strategies using mtDNA analysis: the case of the elusive Mediterranean monk seal (Monachus monachus). Biol Conserv. 2016;193:71–9.
Mekonnen A, Jaffe KE. Bale Mountains monkey Chlorocebus djamdjamensis Neumann 1902. In: Rowe N, Mayers M, editors. All the World’s primates. Charlestown: Pogonias press; 2016. p. 473–4.
Hayaishi S, Kawamoto Y. Low genetic diversity and biased distribution of mitochondrial DNA haplotypes in the Japanese macaque (Macaca fuscata yakui) on Yakushima Island. Primates. 2006;47:158–64.
Liu Z, Wang B, Nadler T, Liu G, Sun T, Huang C, Zhou Q, Zhou J, Que T, Wang Z. Relatively recent evolution of pelage coloration in Colobinae: phylogeny and phylogeography of three closely related langur species. PLoS One. 2013;8:e61659.
Atickem A, Rueness EK, Loe LE, Serbezov D, Bekele A, Stenseth NC. Population genetic structure and connectivity in the endangered Ethiopian mountain Nyala (Tragelaphus buxtoni): recommending dispersal corridors for future conservation. Conserv Genet. 2013;14:427–38.
Gouy M, Guindon S, Gascuel O. SeaView version 4: a multiplatform graphical user interface for sequence alignment and phylogenetic tree building. Mol Biol Evol. 2010;27:221–224.
Dolotovskaya S, Bordallo TJ, Haus T, Noll A, Hofreiter M, Zinner D, Roos C. Comparing mitogenomic timetrees of two African savannah primate genera (Chlorocebus and Papio). Zool J Linnean Soc. 2017;181:471–83.
Edgar RC. MUSCLE: multiple sequence alignment with high accuracy and high throughput. Nucleic Acids Res. 2004;32:1792–7.
Kumar S, Stecher G, Tamura K. MEGA7: molecular evolutionary genetics analysis version 7.0 for bigger datasets. Mol Biol Evol. 2016;33:1870–4.
Hall TA. BioEDIT: a user-friendly biological sequence alignment editor and analysis program for windows 95/98/NT. Nucleic Acids Symp Ser. 1999;41:95–8.
Hasegawa M, Kishino H, Yano T. Dating of the human-ape splitting by a molecular clock of mitochondrial DNA. J Mol Evol. 1985;22:160–74.
Posada D, Buckley TR. Model selection and model averaging in phylogenetics: advantages of Akaike information criterion and Bayesian approaches over likelihood ratio tests. Syst Biol. 2004;53:793–808.
Darriba D, Taboada GL, Doallo R, Posada D. jModelTest 2: more models, new heuristics and parallel computing. Nat Methods 2012;9:772–772.
Bouckaert R, Heled J, Kuhnert D, Vaughan T, Wu CH, Xie D, Suchard MA, Rambaut A, Drummond AJ. BEAST 2: a software platform for Bayesian evolutionary analysis. PLoS Comp Biol. 2014;10:e1003537.
Drummond AJ, Rambaut A. BEAST: Bayesian evolutionary analysis by sampling trees. BMC Evol Biol. 2007;7:214.
Templeton AR, Crandall KA. Sing CF. A cladistic analysis of phenotypic associations with haplotypes inferred from restriction endonuclease mapping and DNA sequence data. III. Cladogram estimation. Genetics. 1992;132:619–33.
Clement M, Posada D, Crandall KA. TCS: a computer program to estimate gene genealogies. Mol Ecol. 2000;9:1657–9.
Leigh JW, Bryant D. POPART: full-feature software for haplotype network construction. Methods Ecol Evol. 2015;6:1110–6.
Nei M. Molecular evolutionary genetics. New York: Columbia University Press; 1987.
Excoffier L, Lischer HE. Arlequin suite ver 3.5: a new series of programs to perform population genetics analyses under Linux and windows. Mol Ecol Resour. 2010;10:564–7.
Mantel N. The detection of disease clustering and a generalized regression approach. Cancer Res. 1967;27:209–20.
Jensen JL, Bohonak AJ, Kelley ST. Isolation by distance. web service BMC Genetics. 2005;6:13.
Yu D, Chen M, Tang Q, Li X, Liu H. Geological events and Pliocene climate fluctuations explain the phylogeographical pattern of the cold water fish Rhynchocypris oxycephalus (Cypriniformes: Cyprinidae) in China. BMC Evol Biol. 2014;14:225.
Li J, Zhao M, Wei S, Luo Z, Wu H. Geologic events coupled with Pleistocene climatic oscillations drove genetic variation of Omei treefrog (Rhacophorus omeimontis) in southern China. BMC Evol Biol. 2015;15:289.
Fu YX. Statistical tests of neutrality of mutations against population growth, hitchhiking and background selection. Genetics. 1997;147:915–25.
Tajima F. Statistical method for testing the neutral mutation hypothesis by DNA polymorphism. Genetics. 1989;123:585–95.
Librado P, Rozas J. DnaSP v5: a software for comprehensive analysis of DNA polymorphism data. Bioinformatics. 2009;25:1451–2.
Harpending H. Signature of ancient population growth in a low-resolution mitochondrial DNA mismatch distribution. Hum Biol. 1994;66:591–600.
Rogers AR, Harpending H. Population growth makes waves in the distribution of pairwise genetic differences. Mol Biol Evol. 1992;9:552–69.
Schneider S, Excoffier L. Estimation of past demographic parameters from the distribution of pairwise differences when the mutation rates vary among sites: application to human mitochondrial DNA. Genetics. 1999;152:1079–89.
Slatkin M, Hudson RR. Pairwise comparisons of mitochondrial DNA sequences in stable and exponentially growing populations. Genetics. 1991;129:555–62.
Drummond AJ, Rambaut A, Shapiro B, Pybus OG. Bayesian coalescent inference of past population dynamics from molecular sequences. Mol Biol Evol. 2005;22:1185–92.
Heller R, Chikhi L, Siegismund HR. The confounding effect of population structure on Bayesian skyline plot inferences of demographic history. PLoS One. 2013;8:e62992.
Grant WS, Liu M, Gao T, Yanagimoto T. Limits of Bayesian skyline plot analysis of mtDNA sequences to infer historical demographies in Pacific herring (and other species). Mol Phylogenet Evol. 2012;65:203–12.
Malukiewicz J, Boere V, Fuzessy LF, Grativol AD, French JA, Pereira L, Ruiz-Miranda CR, Valença YM, Stone AC. Hybridization effects and genetic diversity of the common and black-tufted marmoset (Callithrix jacchus and Callithrix penicillata) mitochondrial control region. Am J Phys Anthropol. 2014;155:522–36.
Rocha S, Perera A, Silva A, Posada D, Harris DJ. Evolutionary history of Trachylepis skinks in the Seychelles islands: introgressive hybridization, morphological evolution and geographic structure. Biol J Linn Soc. 2016;119:15–36.
Thalmann O, Hebler J, Poinar HN, Pääbo S, Vigilant L. Unreliable mtDNA data due to nuclear insertions: a cautionary tale from analysis of humans and other great apes. Mol Ecol. 2004;13:321–35.
Phillips-Conroy JE, Jolly CJ, Brett FL. Characteristics of hamadryas-like male baboons living in anubis baboon troops in the Awash hybrid zone, Ethiopia. Am J Phys Anthropol. 1991;86:353–68.
Jolly CJ, Burrell AS, Phillips-Conroy JE, Bergey C, Rogers J. Kinda baboons (Papio kindae) and grayfoot chacma baboons (P. ursinus griseipes) hybridize in the Kafue River valley, Zambia. Am J Primatol. 2011;73:291–303.
Svardal H, Jasinska AJ, Apetrei C, Coppola G, Huang Y, Schmitt CA, Jacquelin B, Ramensky V, Muller-Trutwin M, Antonio M, et al. Ancient hybridization and strong adaptation to viruses across African vervet monkey populations. Nat Genet. 2017;49:1705–13.
Zinner D, Chuma IS, Knauf S, Roos C. Inverted intergeneric introgression between critically endangered kipunjis and yellow baboons in two disjunct populations. Biol Lett. 2018;14:20170729.
Keller C, Roos C, Groeneveld L, Fischer J, Zinner D. Introgressive hybridization in southern African baboons shapes patterns of mtDNA variation. Am J Phys Anthropol. 2010;142:125–36.
Trosvik P, Rueness EK, de Muinck EJ, Moges A, Mekonnen A. Ecological plasticity in the gastrointestinal microbiomes of Ethiopian Chlorocebus monkeys. Sci Rep. 2018;8:20.
Mekonnen A, Fashing PJ, Bekele A, Hernandez-Aguilar RA, Rueness EK, Stenseth NC. Dietary flexibility of Bale monkeys (Chlorocebus djamdjamensis) in southern Ethiopia: effects of habitat degradation and life in fragments. BMC Ecol. 2018;18:4.
Mekonnen A, Fashing PJ, Sargis EJ, Venkataraman VV, Bekele A, Hernandez-Aguilar RA, Rueness EK, Stenseth NC. Flexibility in positional behavior, strata use, and substrate utilization among Bale monkeys (Chlorocebus djamdjamensis) in response to habitat fragmentation and degradation. Am J Primatol. 2018;80:e22760.
King TE, Jobling MA. Founders, drift, and infidelity: the relationship between y chromosome diversity and patrilineal surnames. Mol Biol Evol. 2009;26:1093–102.
Birky CW, Maruyama T, Fuerst P. An approach to population and evolutionary genetic theory for genes in mitochondria and chloroplasts. and some results Genetics. 1983;103:513–27.
Cords M. The behavior, ecology, and social evolution of cercopithecine monkeys. In: Mitani JC, Call J, Kappeler PM, Palombit R, Silk JB, editors. The evolution of primate societies. Chicago: University of Chicago Press; 2012. p. 91–112.
Bruggeman DJ, Wiegand T, Fernandez N. The relative effects of habitat loss and fragmentation on population genetic variation in the red-cockaded woodpecker (Picoides borealis). Mol Ecol. 2010;19:3679–91.
Ernest E, Haanes H, Bitanyi S, Fyumagwa R, Msoffe P, Bjørnstad G, Røed K. Influence of habitat fragmentation on the genetic structure of large mammals: evidence for increased structuring of African buffalo (Syncerus caffer) within the Serengeti ecosystem. Conserv Genet. 2012;13:381–91.
Billi P. Geomorphological landscapes of Ethiopia. In: Billi P, editor. Landscapes and landforms of Ethiopia. Dordrecht: Springer; 2015. p. 3–32.
Pfeifer SP. The demographic and adaptive history of the African green monkey. Mol Biol Evol. 2017;
Kiage LM, K-b L. Late quaternary paleoenvironmental changes in East Africa: a review of multiproxy evidence from palynology, lake sediments, and associated records. Prog Phys Geogr. 2006;30:633–58.
Chikhi L, Sousa VC, Luisi P, Goossens B, Beaumont MA. The confounding effects of population structure, genetic diversity and the sampling scheme on the detection and quantification of population size changes. Genetics. 2010;186:983–95.
Städler T, Haubold B, Merino C, Stephan W, Pfaffelhuber P. The impact of sampling schemes on the site frequency spectrum in nonequilibrium subdivided populations. Genetics. 2009;182:205–16.
Stone AC, Battistuzzi FU, Kubatko LS, Perry GH, Trudeau E, Lin H, Kumar S. More reliable estimates of divergence times in Pan using complete mtDNA sequences and accounting for population structure. Philos Trans R Soc B. 2010;365:3277–88.
Salvi D, Pinho C, Harris DJ. Digging up the roots of an insular hotspot of genetic diversity: decoupled mito-nuclear histories in the evolution of the Corsican-Sardinian endemic lizard Podarcis tiliguerta. BMC Evol Biol. 2017;17:63.
Ram MS, Kittur SM, Biswas J, Nag S, Shil J, Umapathy G. Genetic diversity and structure among isolated populations of the endangered gees golden langur in Assam, India. PLoS One. 2016;11:e0161866.
Mondol S, Bruford MW, Ramakrishnan U. Demographic loss, genetic structure and the conservation implications for Indian tigers. Proc R Soc B. 2013;280:20130496.
Wayne RK, Shaffer HB. Hybridization and endangered species protection in the molecular era. Mol Ecol. 2016;25:2680–9.
Abbott RJ, Barton NH, Good JM. Genomics of hybridization and its evolutionary consequences. Mol Ecol. 2016;25:2325–32.
Malukiewicz J, Boere V, Fuzessy LF, Grativol AD, e Silva IO, Pereira LC, Ruiz-Miranda CR, Valença YM, Stone AC. Natural and anthropogenic hybridization in two species of eastern Brazilian marmosets (Callithrix jacchus and C. penicillata). PLoS One. 2015;10:e0127268.
Hedrick PW. Adaptive introgression in animals: examples and comparison to new mutation and standing variation as sources of adaptive variation. Mol Ecol. 2013;22:4606–18.
Adams JR, Vucetich LM, Hedrick PW, Peterson RO, Vucetich JA. Genomic sweep and potential genetic rescue during limiting environmental conditions in an isolated wolf population. Proc R Soc B. 2011;278:3336–44.
Hamilton JA, Miller JM. Adaptive introgression as a resource for management and genetic conservation in a changing climate. Conserv Biol. 2016;30:33–41.
Rhymer JM, Simberloff D. Extinction by hybridization and introgression. Annu Rev Ecol Syst. 1996;27:83–109.
Todesco M, Pascual MA, Owens GL, Ostevik KL, Moyers BT, Hübner S, Heredia SM, Hahn MA, Caseys C, Bock DG, Rieseberg LH. Hybridization and extinction. Evol Appl. 2016;9:892–908.
Lawson LP, Fessl B, Hernán Vargas F, Farrington HL, Francesca Cunninghame H, Mueller JC, Nemeth E, Christian Sevilla P, Petren K. Slow motion extinction: inbreeding, introgression, and loss in the critically endangered mangrove finch (Camarhynchus heliobates). Conserv Genet. 2017;18:159–70.
Pfennig KS, Kelly AL, Pierce AA. Hybridization as a facilitator of species range expansion. Proc R Soc B. 2016;283:20161329.
We would like to thank the People’s Trust for Endangered Species and Rufford Small Grants Foundation for covering field work costs and providing equipment to the Bale Monkey Research and Conservation Project. We would also like to thank the Centre for Ecological and Evolutionary Synthesis (CEES) at the University of Oslo and the German Primate Center (DPZ) for providing financial support and facilities for our laboratory analyses. This study would not have been possible without generous funding to Addisu Mekonnen from the Norwegian State Educational Loan Fund (Lånekassen) under the Quota Scholarship program. Peter Fashing thanks the U.S.-Norway Fulbright Foundation for their support during the preparation of this manuscript and San Diego Zoo for their support of his long-term research endeavors in Ethiopia. We would like to thank the Department of Zoological Sciences of Addis Ababa University for logistical support. We are grateful to the Ethiopian Wildlife Conservation Authority for granting permission to conduct this study. We thank Mengistu Birhan, Mamar Dilnesa, Getachew Gutta, Amera Moges and Sewalem Tsehay for their valuable assistance with the field research. We would also like to thank the following local guides and camp attendants: Firdie Sultan, Omer Hajeleye, Hassen Wolle, Jemal Kedir, Mudie Kedir and Matiyos Yakob.
Field work was funded by the People’s Trust for Endangered Species and Rufford Small Grants Foundation. Laboratory work was supported by the Centre for Ecological and Evolutionary Synthesis (CEES), University of Oslo and the German Primate Center (DPZ), Leibniz Institute for Primate Research.
Availability of data and materials
All sequence data generated from this study have been deposited in GenBank and are available under accession numbers MG786940 - MG787070. All other data are included in this manuscript and its supplementary information files.
Ethical approval and consent to participate
Consent for publication
The authors declare that they have no competing interests.
Springer Nature remains neutral with regard to jurisdictional claims in published maps and institutional affiliations.
Comparison of the phenotypic appearance of typical Bale monkeys, vervets, and their putative hybrids. (a) Adult putative vervet at Kokosa possibly the father of the hybrid. (b) Adult female Bale monkey and a putative juvenile hybrid of Bale monkey (♀) × vervet (♂) at Kokosa. A putative hybrid at Kokosa (c, d) with an intermediate coat colour that is more golden than that of a Bale monkey but less golden than that of a vervet. The animal shows a white browband, though it is smaller than that of a vervet and nearly absent in Bale monkeys. The hybrid has an intermediate tail length and face colour, the face is darker in vervet but lighter in Bale monkey. However, this hybridization event is most likely as a consequence of the release of a pet vervet in the range of the FF population [J.-M. Lernould, personal communication]. (e, f) Adult vervet from Gonosa, Robe District with more golden fur, hands and feet are very dark, thick white browband, long and white whiskers, dark face with golden moustache, and long tail with black tip. (g, h) Adult Bale monkey in CF of Odobullu Forest exhibits a relatively brown/grey coat, lacks a white browband, whiskers are short, front neck covered with white fur, hands and feet blackish brown, and relatively short tail . Bale monkey in FF of Kokosa (i) and Afura (j) that are phenotypically more similar to CF population (g, h) than that of grivet  and vervet (e, f). (DOCX 5055 kb)
Summary of sampling localities and number of samples. (DOCX 24 kb)
Summary of haplotype distribution of Chlorocebus species. (DOCX 23 kb)
FST values (p values) of pairwise comparisons among 12 Bale monkey localities. (DOCX 26 kb)
About this article
Cite this article
Mekonnen, A., Rueness, E.K., Stenseth, N.C. et al. Population genetic structure and evolutionary history of Bale monkeys (Chlorocebus djamdjamensis) in the southern Ethiopian Highlands. BMC Evol Biol 18, 106 (2018). https://0-doi-org.brum.beds.ac.uk/10.1186/s12862-018-1217-y
- Genetic diversity
- Gene flow
- Mitochondrial DNA
- Habitat fragmentation