Mind the gaps: investigating the cause of the current range disjunction in the Cape Platanna, Xenopus gilli (Anura: Pipidae)

Study species and sampling

Xenopus gilli, the Cape platanna, inhabits lowland acid blackwater pools characteristic of the fynbos biome (Picker & de Villiers, 1989). Anthropogenic disturbances, intense urbanisation and the spread of alien vegetation has resulted in declines of populations of X. gilli, so that this species is now considered Endangered (SA-FRoG & IUCN SSC-ASG, 2011). Xenopus gilli was initially known from only two localities (the Cape Peninsula and adjoining Cape Flats) but in the 1970s a population was discovered approximately 50 km to the east, on the opposite side of False Bay (see Fig. 1A). Lastly, in 1987 a third disjunct cluster of sites was found near the town of Pearly Beach (Picker & de Villiers, 1989, Fig. 1). The Cape Flats were farmed for more than two centuries, and it is postulated that this resulted in the reduction of X. gilli populations (Kobel, Du Pasquier & Tinsley, 1981; Picker, 1985; Picker & de Villiers, 1989; Simmons, 1985). However, more recent urbanisation of the Cape Flats over the last 50 years (see Rebelo et al., 2011), would have extirpated any remaining populations. In addition to loss of habitat through land use change, X. gilli is threatened through introgression from its sister species, Xenopus laevis (Daudin) (see Picker & de Villiers, 1989) which is known for its invasive abilities on four continents (Measey et al., 2012). In South Africa, X. laevis is considered to be a domestic exotic, readily invading disturbed waters, and it is present throughout the entire range of X. gilli (Measey & Channing, 2003; Measey & Davies, 2011).

Morphological intermediates between these two Xenopus species from the Cape of Good Hope Nature Reserve (COGH: at the tip of the Cape peninsula: see Fig. 1) were first noted by Rau (1978). The severity of the threat of extensive introgression was questioned due to the low fitness and reproductive capability of any hybrid offspring that were produced (Picker, 1985), and later by the low frequency of genetically hybrid individuals (Evans et al., 1997). Although studies incorporating molecular genetics suggested that there was relatively little hybridization present between the two species (Evans et al., 1997; Evans et al., 1998), the threat posed by X. laevis remains of conservation concern (Measey, 2011; SA-FRoG & IUCN SSC-ASG, 2011).

Xenopus gilli was first described from the Silvermine River (Rose & Hewitt, 1927) and is usually characterised by a venter marked with bright yellow-orange and black mottling; although this is more distinct in some animals than others (de Villiers, 2004). Dorsally, X. gilli is yellow-brown or beige with large paravertebral dark brown stripes extending from the eyes, down the length of the body and breaking up into patches on the lower back and legs. They exhibit sexual size dimorphism with the larger females attaining a snout-vent length of approximately 60 mm and having distinct cloacal folds (de Villiers, 2004; Kobel, Loumont & Tinsley, 1996).

For this study, netted funnel traps baited with liver were set overnight and retrieved in the early morning on two consecutive days of each field excursion (see Measey, 2001), from March 2010 to August 2011. In addition to traps, seine nets were used at some localities during operations to remove X. laevis (see Measey & Davies, 2011). Collections of Xenopus were made at eight ponds across the three different areas. Three ponds were sampled on the Cape peninsula (in the Cape of Good Hope Nature Reserve: CoGH), all within an area of 2 km². All other collection sites were on the east side of False Bay (Fig. 1A) at ponds where X. gilli historically occurred (see Picker & de Villiers, 1989). Xenopus gilli were captured near Kleinmond (three ponds; hereafter Kleinmond) and near Pearly Beach (two ponds; hereafter Pearly Beach). We identified individuals as X. gilli from dorsal and ventral patterning, shape of head, and overall size (de Villiers, 2004; Kobel, Loumont & Tinsley, 1996). Xenopus laevis and suspected X. gilli-laevis hybrids were not included in our analyses.

Each X. gilli captured had the second phalange of the right hind foot clipped, taking care to not break the webbing between the toes. Blades were sterilised with 10% bleach solution between each procedure to prevent any spread of disease. Tissue samples for DNA analysis were stored in vials of molecular grade ethanol.

Permits were obtained from Cape Nature (permit number: AAA004-00322-0035) and South African National Parks (permit: Agulhas and Table Mountain National Parks, issued 21 July 2010). Ethics clearance was obtained from South African National Biodiversity Institute ethical clearance (number: 001/10).

Morphometrics

All Xenopus gilli captured had a standard set of 14 measurements taken: snout-vent length (SVL), head length (HL), head width (HW), head height (HH), lower jaw length (LJL), ilial length (IL), ilial width (IW), femur (FM), tibia (TB), metatarsal (MT), longest toe (LT) on the hind limb, humerus (HM), radius (RD), and longest finger (LF) on the forelimb (see Herrel et al., 2012). All measurements were taken by DJF with digital callipers (with 0.01 mm accuracy) on the left side of each animal. In addition, images were taken of the dorsum and venter of each animal on scaled grid paper to avoid measuring animals recaptured.

Genetics

Total genomic DNA was extracted from the tissue samples using a standard salt extraction procedure (Bruford et al., 1992) and fragments of two mitochondrial (mt) markers (ND2 and 16S) were amplified. However, as mtDNA is non-recombinant and is maternally inherited (Lamb & Avise, 1986) our analysis is limited to inferences based on the maternal lineage, specifically with regards to identifying any hybridization with X. laevis. The ND2 marker was amplified from vMet3 to vTrp (Cunningham & Cherry, 2004) and 896 base pairs were used for analysis (mtDNA BP 5980 to 6876, Roe et al., 1985). Polymerase chain reaction (PCR) annealing temperature was optimised at 57.1°C for 40 cycles and magnesium concentration was 3 mM MgCl₂. The 16S marker was amplified from primers 16Sa to 16Sb (Palumbi, 1996) of which 517bp were used for analysis (mtDNA BP 4052 to 4559, Roe et al., 1985). PCR annealing temperature was optimised at 48.1°C for 40 cycles and magnesium concentration was 2.5 mM MgCl₂. Electrophoresis was used to examine the quality of PCR products on a 2% agarose gel stained with Goldview and the high quality products were sent to Macrogen Inc. (Seoul, Korea) for sequencing.

Data analysis

Geneious Pro 5.0.4 was used to edit and align the DNA sequences from each sample using a global alignment (Drummond et al., 2007) and the alignment was used to define haplotypes at each site. One animal from Cape Point was removed from all further analyses as it fell into an eastern haplotype population. Similarly, Evans et al. (1997) found another such animal in their study and speculated that it may have been mistakenly transported and introduced. Any other individuals that closely matched X. laevis (i.e., had >98% alignment with the ND2 region of EMBL accession HM991335) were considered to be hybrids and therefore removed from further analyses.

In order to determine whether sampling sites clustered on a population level, a spatial analysis of variance (SAMOVA) was conducted (Dupanloup, Schneider & Excoffier, 2002), using ND2 haplotype data and geographic co-ordinates of each of the 9 sample sites. The SAMOVA was run for K = 2–9 putative populations to determine the maximum F_CT value, the highest proportion of differences between populations due to genetic variation (Dupanloup, Schneider & Excoffier, 2002). The results of the SAMOVA allowed for the consolidation of the DNA data into a Cape peninsula population and a combined Kleinmond and Pearly Beach population for further genetic and morphometric analyses (henceforth combined and referred to as the “eastern population”). Network 4.5.1.6 (Bandelt, Forster & Röhl, 1999) was used to consolidate the haplotype data into a Median-joining network. Arlequin 3.5 (Excoffier & Lischer, 2010) was used to provide a quantitative measure of haplotype and nucleotide diversity within localities. Sequence divergence between populations was estimated with uncorrected net p-distances using MEGA v. 5 (Tamura et al., 2011).

To examine whether any population had experienced historical demographic changes, Tajima’s D and Fu’s F_S was used to test for departures from mutation–drift equilibrium (Chuang & Lee, 1997; Schneider & Excoffier, 1999) using Arlequin 3.5 (Excoffier & Lischer, 2010). For populations out of equilibrium, we then applied a model of demographic expansion (Excoffier & Lischer, 2010; Rogers, 1995; Rogers & Harpending, 1992). For populations that showed signs of expansion, we estimated the timing of the demographic shift; t = τ/(2u), where t is time in generations, τ is the age of the expansion in mutational units (estimated in the model of demographic expansion) and u is the sum of the per nucleotide mutation rate for the region sequenced (Rogers, 1995; Rogers & Harpending, 1992). For the present study, generation time was estimated at 2 years (de Villiers, 2004) and u was obtained from the same estimate of mutation rate as described for coalescence analysis (below).

Coalescent analysis was used to investigate time of divergence (t) between all the populations identified in SAMOVA (Cape Peninsula vs. eastern), using IMa2 (Hey, 2010). IMa2 runs Markov chain Monte Carlo (MCMC) simulations using a likelihood based analysis, under a Felsenstein framework (Hey & Nielsen, 2007). MCMC included a burn-in duration of 3 million steps, 10 000 genealogies saved and a geometric heating model with 20 chains, 0.96 as first and 0.9 as second chain heating parameters. A geometric heating scheme was applied to ensure sufficient rates of chain swapping to speed up the calculation process. The mutation rates for the ND2 and 16S regions of the mitochondrion were determined using the estimated time of divergence reported for the dated time of divergence between the two X. gilli lineages (8.5 Mya) in Evans et al. (2004). Mutation rate was estimated to be 0.52% change per lineage per million years, and compares favourably with other mutation rates published for ND2 (e.g., 0.69% Macey et al., 1998). For 16S, we used the same calculation to give us a rate of 0.10% change per lineage per million years, which is in the same general range as other published rates for this marker (e.g., 0.15% Vences et al., 2005). The software IMa2 uses the geometric mean of all mutation rates with upper and lower confidence intervals which were calculated from the upper and lower divergence bounds for X. gilli: 4.8 and 13.4 Mya (Evans et al., 2004). Preliminary runs in IMa2 were used to establish settings for priors, ensure adequate mixing and sufficiently high effective sample size (see Hey, 2010), this included setting migration to 0 between CoGH and other populations due to an absence of shared haplotypes between populations. Three final duplicate runs were made with the same parameters using IMa2 at Cornell University via internet upload (http://cbsuapps.tc.cornell.edu/IMa.aspx).

For the morphological analysis, all measurements were Log₁₀-transformed to meet assumptions of homoscedascity, and then residuals were estimated for 13 variables against SVL to correct for size because amphibians are known to have indeterminate growth and thus their size positively correlates with age (Halliday & Verrell, 1988), including species in the genus Xenopus (Measey, 2001). To examine sexual dimorphism, a multivariate analysis of variance (MANOVA) was performed in the base package of R (R Development Core Team, 2011) using the residuals of morphometric data, separately for each genetically defined population (Cape peninsula and eastern). In addition, we checked for sexual differences within populations by using the locality and sex as an interaction term.

In the absence of sexual dimorphism for the variables measured (see Results), data from both sexes were pooled for all further analyses. To examine population level differences in morphology, a multivariate approach was taken. Size corrected residuals from the Cape peninsula (n = 50) and from the eastern population (n = 59) were used as input variables for a principal components analysis (PCA) to reduce the 13 morphometric variables into linear combinations of correlated variables (principal components-PCs). The Keiser-Meyer-Olkin (KMO) measure of sampling adequacy was applied to determine whether the dataset was adequate to conduct a PCA. The analysis included a varimax rotation to minimise the number of variables with high loadings on each PC, which simplifies the interpretation of the PCs extracted. Variables with communalities greater than 0.5 were retained in the analysis and only PCs with eigenvalues greater than 1.0 were extracted. The principal component scores were saved, and ANOVA was carried out on the PCs extracted using R (R Development Core Team, 2011).

Genetics

Sequences of 896 base pair fragment of ND2 were obtained from 128 individuals identified in the field as X. gilli, plus 517 bp of 16S from a subset of 14 animals. Of the 39 X. gilli collected and sequenced for ND2 from the Cape peninsula, one was found to match a GenBank X. laevis sequence. From the 48 sequenced animals from Pearly Beach, four ND2 haplotypes matched X. laevis, but for the Kleinmond sample, this proportion reached 27% of 41 animals sequenced (Table 1). All animals with X. gilli appearance, but with X. laevis haplotypes were subsequently removed from genetic and morphometric analysis. Spatial clustering analysis (implemented in SAMOVA) unambiguously showed that the nine sampling sites could be grouped into two populations, corresponding to animals collected in the Cape peninsula (western) and combined eastern sites (Kleinmond and Pearly Beach: FST = 0.985; P < 0.001). For 16S, all four individuals sequenced from the Cape peninsula were of a single haplotype identical to X. gilli from Cape Point sequenced by Evans et al. (2004, AY581649). Of ten animals sequenced from the eastern region, eight were identical to an X. gilli previously sequenced from Betty’s Bay by Evans et al., (2004, AY581650), while two more individuals (both from Kleinmond) had a single base pair change. Between the Cape peninsula (within 0.00% divergence) and eastern sites (within 0.069% divergence), the net p-distance for 16S was found to be 1.7%.

The haplotype network for ND2 shows two clear groups separated by 74 base pair changes (Fig. 2). Sequence divergence between populations shows a net p-distance of 8.8% at the ND2 locus between animals from the Cape peninsula and the eastern population. The Cape peninsula had only three ND2 haplotypes amongst 38 individuals (p-distance within = 0.25%), while the 74 animals sequenced from the eastern population share 30 different haplotypes (p-distance within = 5.63%).

The eastern X. gilli populations had a higher ND2 nucleotide and haplotype diversity than animals from the Cape peninsula (Table 2). However, the 95% confidence intervals show that the Cape peninsula population is significantly less diverse for haplotype diversity (h), but not nucleotide diversity (π). The low haplotype diversity on the Cape peninsula is also demonstrated by the haplotype network (Fig. 2A). Both Tajima’s D and Fu’s F test suggest that the eastern population is out of mutation-drift equilibrium (Tajima’s D = −1.6, p = 0.032; Fu’s F_S = −27.2, p < 0.001), but this was not detectable within the Cape peninsula. The model of demographic expansion fitted the observed distribution for the eastern population (SSD = 0.005, p = 0.08) suggesting the population has undergone a demographic shift. The value obtained for τ = 2.16 (95% CI: 1.29–2.78), provided an estimate for years since population expansion (t) of 75.7 thousand generations or ca. 151.4 Kya.

The coalescent analysis provided an estimated divergence time between the Cape peninsula and eastern population of ca. 4.6 Mya with a confidence interval from 3.2 to 6.4 Mya (Table 2; Fig. 3), which falls entirely within the Pliocene.

Morphometrics

Morphometric measures were made on a total of 109 individuals from all sites. Following the results of SAMOVA analysis we conducted morphometric tests on animals collected from all eastern populations (Pearly Beach and Kleinmond; n = 59) compared to those from the Cape peninsula (n = 50). The first test for sexual size dimorphism confirmed that in both populations females were significantly larger than males by around 25%: Cape Peninsula females had a mean SVL of 43.0 mm (SE 0.752), while males’ was 34.6 mm (SE 0.528; t_1,48 = −7.248; P < 0.001). For the eastern population, mean female SVL was 44.2 mm (SE 0.071), with males’ mean of 34.3 mm (SE 0.618; t_1,57 = −8.88; P < 0.001). No significant differences were found overall between sexes using size corrected measurements in a MANOVA (Pillai = 0.1250, P = 0.42). Additionally, there was no significant difference for the interactive term: sex and population (Pillai = 0.1692, P = 0.15), indicating that within populations, the sexes did not differ in their morphology. Thus, for all further tests sexes were pooled.

Four principal components (PCs) were extracted in the PCA, which accounted for 73.3% of the total variation in the dataset (Table 3). The KMO test indicated sampling was adequate (KMO = 0.83), all communalities were high suggesting that all variables were reliable contributors to the analysis. The four PCs extracted (Table 3) loaded highest with measures of the limbs and head (metatarsal, head width, femur, ilial width, tibia, longest toe and head height in descending order) on PC1 (Fig. 4), and arm and ilial length (radius, ilial length, longest finger) on PC2. An analysis of variance (ANOVA) on the principal components showed significant differences between the populations for PC1 only (PC1 F_107,1 = 180; P < 0.0001, PC2 F_107,1 = 1.503, P = 0.2228; Fig. 4D) suggesting that they can be distinguished on the basis of limb dimensions and head height.

Historical events

Inundation of the Cape Flats was previously speculated to have caused the deep genetic division in the Cape Xenopus lineage (Evans et al., 1997), but repeated inundations both pre- and post-date our estimated divergence time (Compton, 2011), and so it seems unlikely that sea-level changes can be the sole factor responsible for the divergence. Sea-level change may have produced two different scenarios for these two Xenopus lineages: sea-level rises which contracted populations and sea-level falls which may have allowed a range extension and migration (cf Schreiner, Roedder & Measey, 2013). Furthermore, we suggest that the effects of climate change from 5 Mya are of key importance, when substantial uplifting led to significant reduction of rainfall in this area (McCarthy & Rubidge, 2005), reduction in temperature (Zachos et al., 2001) and a massive expansion in regional floristic diversity (Cowling, Proches & Partridge, 2009).

The Agulhas Bank was last exposed as recently as the last glacial maximum, some 20 Kya with a sea-level fall of around 140 m (Compton, 2011). The change in climate and land area since then is predicted to have had a major reduction on the distributions of Cape frogs (Schreiner, Roedder & Measey, 2013). At the last glacial maximum, much of the exposed land would have been sand fynbos vegetated dunes similar to that seen, and not occupied by X. gilli, on the Cape Flats today (see Compton, 2004). East of False Bay, the extension of the rivers across the exposed southern coastal plain would have in part coincided with bedrock supporting both Renosterveld and lowland sand-stone fynbos, vegetation types on which X. gilli are found today (Fig. 1B). On the Cape peninsula, it seems that only a small amount of land to the West and South would have been exposed, and this would also have been the currently uninhabited sand fynbos. Due East of the Cape peninsula (5–10 km) lies a large (approximately 50 km²) outcrop of sandstone which may have been able to support a population of X. gilli. It is not known whether X. gilli would have been capable of movement across the intermediary habitat, and there is a similar distance from this outcrop to the habitat extensions in the east. If dispersal was possible over these distances, there is the potential for movement of individuals across False Bay at each glacial maximum. Similarly, Rourke (1972) speculated about the dispersal of Proteacae across the same bridging habitat.

Our molecular data does not exclude movement between these lineages, as we did find a single individual in the Cape peninsula with a haplotype from the western population, as did Evans et al. (1998 see below). If single animals are capable of dispersal on this scale, our interpretation that this resulted from the release of captive animals would be erroneous. We suggest that in the east, as continuous appropriate habitat would have been uncovered by the retreat of the sea during the last glacial maximum (Fig. 1B), that this Xenopus lineage would have had a larger distribution. This may explain the star-shaped haplotype network (Fig. 2), and the significant results of neutrality tests, which suggest that this lineage has undergone recent expansion. Using mutation rates already described for ND2, we date this expansion to around 150 Kya, a period when the Agulhas bank was exposed with sea-level some 140 m lower than today (Compton, 2011).

Our approximate dates for divergence between the populations coincide with a period when sea-level is hypothesised to have been around 25 m higher (also see Raymo et al., 2011). However, unless this was the first marine incursion in the area, there is no reason to think that the substrate immediately prior (or after) to this time was any more suitable than it is today. Certainly the sea also covered the Cape Flats 1.5 Mya (Compton, 2004), and was even 20 m higher than current levels around 130 Kya (Compton, 2011). Thus, if sea-level has repeatedly covered the Cape Flats and uncovered the Agulhas Bank throughout the Pleistocene period, we look to other explanations for the continued separation of these lineages.

We consider that composition of the underlying substrate may be more likely to have had a lasting effect on the distribution of these acidophilic species. Distribution records for X. gilli suggest that this species is not tolerant of alkaline substrates, such as those currently in place over much of the Cape Flats area today (see Fig. 1B, Picker & de Villiers, 1989). The alkalinity of this area is thought to be in part due to repeated marine incursions, but with additional calcareous wind-blown sands resulting from the erosion of uplifted material (Compton, 2004; Cowling, Proches & Partridge, 2009). This suggests that areas that had been suitable for the ancestor of these populations were continually reduced over the last 5 My.

Climatic change also followed this period of substantial uplifting on the eastern side of the subcontinent and is thought to have led to significant reductions of rainfall in the west and aridification of the interior of South Africa (McCarthy & Rubidge, 2005; Partridge & Maud, 2000). The start of these substantial changes, around 5 Mya, coincides with our estimated split within Xenopus gilli and the rapid diversification and establishment of the fynbos biome ca. 3–5 Mya (Cowling & Pressey, 2001; Goldblatt, 1997), on whose acid-blackwaters X. gilli now depends (Picker, 1985). This same period is known to have resulted in radiations of other faunal groups in this specific area of the south-western Cape (e.g., Smit, Robinson & Van Vuuren, 2007; Swart, Tolley & Matthee, 2009; Tolley, Chase & Forest, 2008; Tolley et al., 2010). Thus, the tectonic uplift began a series of processes (spread of alkaline substrate and drying) which reduced the range of the most recent common ancestor of these distinct lineages, eventually leading to their divergence around 4.63 Mya. Further, we postulate that these processes, which have been ongoing, continue to reduce the ranges of these lineages (and other species such as Microbatrachella capensis), and this might explain why there was not a more recent genetic expansion during the last glacial maximum. Most recently however, anthropogenic factors have further reduced the ranges of these X. gilli populations, raising concern for the conservation of these species.

Conservation

On the Cape peninsula, there has been a reduction in the known range of Xenopus gilli over the past century. The type series was said to be collected from the Silvermine River and adjacent Cape Flats (Rose & Hewitt, 1927), and in the same publication, it was noted that frogs collected from these localities were already outnumbered by X. laevis (see also de Villiers, 2004). The last record of this species outside of the CoGH is a specimen collected at Zeekovlei in the mid-1970s (in the Iziko Museum, Cape Town: Picker & de Villiers, 1989). This dramatic and rapid reduction in range may in part explain the low haplotype diversity observed in population sampled from the Cape peninsula (see also Cressey, Measey & Tolley, in press). The disparity between haplotype (h) and nucleotide (π) diversity between the two lineages is indicative of a bottleneck in the Cape peninsula, with a reduction in the number but not in the diversity of the remaining haplotypes. The distribution of pairwise differences between haplotypes (Fig. 2B) is also suggestive that intermediary haplotypes have been lost. The scenario is similar to that described in other historically documented cases of population bottlenecks (Hoelzel et al., 2002; Weber et al., 2000).

Natural hybridisation between Xenopus laevis and X. gilli was reported as far back as the 1970s (Kobel, Du Pasquier & Tinsley, 1981; Picker, 1985; Picker & Samways, 1996; Rau, 1978; Simmons, 1985), although continuing investigations showed that hybrid males were not fertile, and hybrid females had a reduced fecundity (Gurdon, 1996). The first genetic investigations into the frequency of hybrids found only a single (nuclear) hybrid in 32 X. gilli (and 38 X. laevis) sampled in the eastern area, while none were found from 59 sampled from the CoGH reserve (Evans et al., 1998). Thus, these authors concluded that introgression was not the greatest obstacle to X. gilli conservation. Our study, sequencing mtDNA only, avoided sampling any obvious X. laevis or putative X. laevis-gilli hybrids, but still found substantial numbers of animals which were morphologically identified as X. gilli (see methods for characters) but result from a X. laevis maternal lineage. From relatively low levels (2.5%) on the Cape peninsula, to 27% in ponds near Kleinmond where X. laevis and hybrids have come to dominate some historically known X. gilli sites. Ponds near Pearly Beach, which were previously thought to contain only pure X. gilli (see Evans et al., 1998; Picker & de Villiers, 1989), were found to have 8% hybrids, even though no X. laevis-like animals were seen. Our results suggest that hybridisation has greatly increased in both lineages and this aspect requires better investigation using nuclear markers and larger sample sizes.

Although we decided to remove the single individual found in CoGH with the eastern haplotype from our analysis, there remains the question surrounding the provenance of this individual with a haplotype also found by Evans et al. (1997). There are two possibilities: first that this individual was anthropogenically introduced into CoGH, or second that it represents ancient migration from the eastern population to the west. We reason that if it was possible for animals to migrate east to west, then the return route should also have been possible, and we might therefore expect to see instances of peninsula haplotypes in eastern populations. Given that the last time that the Cape Flats were covered was some 1.5 Mya (Compton, 2004), migrants from that time should be discernible from modern movements through further genetic testing such as micro-satellites. It is important to conduct such a test as otherwise these animals present another introgression threat to the remaining population on the peninsula.

Lastly, we suggest that the eastern lineage of X. gilli requires taxonomic attention through data on calls, patterning and lateral line configuration. Despite recent conservation work at CoGH removing hundreds of Xenopus laevis, hybridisation poses an ongoing threat (see Measey & Davies, 2011). The eastern population occurs over a much wider area, but all of this is threatened by invasive alien plants (as well as hybridising X. laevis). Despite good and clear documentation on the threats to this species, all appear to continue unabated.