This paper contains supplementary material that can be found online at http://journals.cambridge.org
Introduction
Populations of many frogs have declined alarmingly in recent years, placing nearly one third of the > 6,000 species under threat of extinction (IUCN, 2010). Declines have been attributed largely to habitat loss, environmental degradation and/or infectious diseases such as chytridiomycosis (Stuart et al., Reference Stuart, Hoffman, Chanson, Cox, Berridge, Ramani and Young2008; Kilpatrick et al., Reference Kilpatrick, Briggs and Daszak2010). Many frogs undergo dramatic natural population fluctuations (e.g. Pechmann et al., Reference Pechmann, Scott, Semlitsch, Caldwell, Vitt and Gibbons1991; Semlitsch et al., Reference Semlitsch, Scott, Pechmann, Gibbons, Cody and Smallwood1996) such that long-term data are required to determine population trends without undue influence of stochastic factors (e.g. Meyer et al., Reference Meyer, Schmidt and Grossenbacher1998; Marsh, Reference Marsh2001; Green, Reference Green2003). Long-term quantitative data are generally lacking for the vast majority of frog species, particularly in the tropics (Adeba et al., Reference Adeba, Kouassi and Rödel2010; Largen & Spawls, Reference Largen and Spawls2010). For Africa this is exacerbated by a general relative scarcity of attention to conservation biology research despite many threats to its globally important biota (Pimm, Reference Pimm2007). Here we present long-term quantitative data for four frog genera endemic to an Afromontane region of exceptional importance but growing conservation concern.
The Bale Mountains lie in southern Ethiopia, east of the Rift Valley (Fig. 1). The Mountains are a high (up to nearly 4,400 m) and extensive massif with rich biodiversity, including many unique, rare, spectacular and threatened taxa. Hillman (Reference Hillman1986: 255) considered the Mountains ‘a centre of faunal endemicity, probably with the highest rate of animal endemicity for a terrestrial habitat anywhere in the world’. The region incorporates the largest single area (> 4,000 km2) in Africa over 3,000 m altitude, and is a crucially important reservoir of globally threatened Afromontane and Afroalpine habitats (Largen & Spawls, Reference Largen and Spawls2010).
Fig. 1 Map of the Bale Mountains National Park, Ethiopia showing Park boundary, local villages and towns (squares), and sampling localities A–H (dots) referred to in the text and Table 1. The dots labelled A2 to A5 are based on coordinates given in error by Grandison (Reference Grandison1978) and Largen (Reference Largen2001); these localities are actually close to the Goba–Rira road, approximately within the area marked by the ellipse labelled A2–A5. Rira, in the centre of the Park, is at 6.771°N, 39.725°E.
The highest part of the region, the Sanetti Plateau and associated peaks, comprises Afroalpine grasslands with a highly endemic biota. To the south, the Sanetti Plateau terminates at the Harenna escarpment that drops from 3,200 to 2,000 m in 8 km. This escarpment exhibits a dramatic vegetation zonation from the plateau grasslands through low heather scrub, giant heather (Erica spp.) forest, Hagenia, bamboo and Podocarpus forest, high altitude woodland and into medium altitude rainforest (Friis, Reference Friis1986; Miehe & Miehe, Reference Miehe and Miehe1993, Reference Miehe and Miehe1994). This is one of the largest natural areas of forest remaining in Ethiopia. Towards the west, north and east the Sanetti Plateau falls away more gently and change in vegetation is less abrupt, with Afroalpine grasslands giving way to heather moorlands and, below c. 3,000 m, Hagenia forest.
A substantial area (c. 2,200 km2) of the region is covered by the Bale Mountains National Park, established in 1971 but not yet formally gazetted by the Ethiopian government. The Park is the most important conservation area in Ethiopia (Frankfurt Zoological Society, 2007), one of the most important in Africa (Largen & Spawls, Reference Largen and Spawls2010), and one of 34 Conservation International global biodiversity hotspots. The Park is a BirdLife International Important Bird Area, and on the Tentative List to qualify as a World Heritage Site. Many people live and exploit natural resources within the Park, and their activities are the primary threat to the native biodiversity (Frankfurt Zoological Society, 2007). Conservation efforts are currently focused on habitats, and on flagship threatened bird and mammal species, which are concomitantly the taxa that are best known scientifically. For example, the Park is the focus of the Ethiopian Wolf (Canis simensis) Conservation Programme (e.g. Sillero-Zubiri et al., Reference Sillero-Zubiri and Macdonald1997; Atickem et al., Reference Atickem, Bekele and Williams2009), and the main remaining stronghold of the mountain nyala Tragelaphus buxtoni (Malcolm & Evangelista, Reference Malcolm and Evangelista2005) and Bale monkey Chlorocebus djamdjamensis (Mekonnen, Reference Mekonnen2008; Mekonnen et al., Reference Mekonnen, Bekele, Hemson, Teshome and Atickem2010). The Park is important as a water source for c. 12 million people and of outstanding social, scenic and cultural value (Hillman, Reference Hillman1988; Frankfurt Zoological Society, 2007). A management plan for the Park was published recently (Frankfurt Zoological Society, 2007).
About 15 amphibian species (all anurans) have been reported from the Bale Mountains, including 10 endemics (Largen, Reference Largen2001; Largen & Spawls, Reference Largen and Spawls2010). The Bale Mountains National Park is an Alliance for Zero Extinction site, partly because of its endemic amphibians (Alliance for Zero Extinction, 2010). Given the Park's importance for their conservation we focus here on four monotypic frog genera: all endemic to Ethiopia and three endemic to the Bale Mountains.
Previous work up to 1986
Although there is a long history of human habitation in the area, the Bale Mountains remained largely unexplored scientifically until the middle of the 20th century. The Chicago Field Museum's W.H. Osgood collected some amphibians and reptiles in 1926–1927. Partly in association with other British colleagues, M.J. Largen carried out extensive collections between 1971 and 1975. Early expeditions were centred around Dinsho/Dinshu and the northern slopes below the Sanetti Plateau. In 1983 it become feasible to reach the Harenna Forest on the southern side of the massif by road. Conscious of the conservation threat posed by the new road the Ethiopian Wildlife Conservation Organization arranged an expedition with Addis Ababa University to conduct a preliminary survey of the Harenna Forest in August 1986.
We follow the taxonomy of the latest comprehensive treatment of Ethiopian amphibians (Largen, Reference Largen2001; Largen & Spawls, Reference Largen and Spawls2010). The localities reported for Spinophrynoides, Altiphrynoides and some other Bale Mountain frogs as south-east of Goba (Grandison, Reference Grandison1978; Largen, Reference Largen2001) are in error. These localities are south of Goba along the Goba–Rira road; the reported altitudes are approximately correct but the coordinates are not.
Focal species
Fuller accounts of the systematics, natural history and conservation biology of the four species are given in Appendix 1.
Spinophrynoides osgoodi (Plate 1a) was described in 1932 from specimens collected between 1926 and 1927, from an imprecise type locality (‘Gedeb Mountains’, Loveridge, Reference Loveridge1932). It has been recorded in Ethiopia from beyond the Bale Mountains but the vast majority of records are from north and south of the Sanetti Plateau, typically in montane forest but extending also into open moorland at 1,950–3,520 m (Largen, Reference Largen2001). It is a small to medium (snout–vent length to 62 mm) species that lays strings of eggs in small pools that develop into tadpoles before metamorphosing into froglets (Grandison, Reference Grandison1978; Largen, Reference Largen2001). The presence of this Ethiopian endemic genus in the Bale Mountains has been overlooked by some non-herpetologists and conservation managers (e.g. WCMC, 1993; Miehe & Miehe, Reference Miehe and Miehe1994) because S. osgoodi was not classified in the genus Spinophrynoides until 1987. It has been categorized as Vulnerable on the IUCN Red List since the first Global Amphibian Assessment in 2004 (Stuart et al., Reference Stuart, Hoffman, Chanson, Cox, Berridge, Ramani and Young2008; IUCN, 2010).
Plate 1 The four endemic Ethiopian monotypic frog genera studied: (a) Spinophrynoides osgoodi, (b) Altiphrynoides malcolmi, (c) Ericabatrachus baleensis, and (d) Balebreviceps hillmani. S. osgoodi is endemic to the highlands of Ethiopia; the others are endemic to the Bale Mountains. (a) by S. Spawls, (b–d) by M. Menegon.
Altiphrynoides malcolmi (Plate 1b) was described in 1978 from > 160 specimens collected between 1971 and 1975 from the northern side of the Sanetti Plateau. The species was collected subsequently from the Harenna escarpment. It is endemic to the Bale Mountains, reported from altitudes of 3,200–4,000 m, spanning the upper limits of the Schefflera–Hagenia–Hypericum forest to Afroalpine moorland (Largen, Reference Largen2001). This small species (snout–vent length < 32 mm, Largen, Reference Largen2001) has internal fertilization and lays small clutches of large eggs communally in moist terrestrial sites that hatch into non-feeding tadpoles that remain on land (Grandison, Reference Grandison1978). Because A. malcolmi has been classified in Altiphrynoides only since 1987 the presence of this endemic genus has been overlooked in some summaries of the fauna (e.g. WCMC, 1993; Miehe & Miehe, Reference Miehe and Miehe1994). It has been categorized as Endangered on the IUCN Red List since the first Global Amphibian Assessment in 2004 (Stuart et al., Reference Stuart, Hoffman, Chanson, Cox, Berridge, Ramani and Young2008; IUCN, 2010).
Ericabatrachus baleensis (Plate 1c) is endemic to the Harenna escarpment and was described in 1991 from specimens collected in 1986. Twenty-two of the types were collected from the margins of a stream in giant Erica forest at the type locality (Tulla Negesso) for Balebreviceps hillmani (see below) at 3,200 m, with one specimen coming from a stream at Katcha, at 2,400 m. We know of no published records beyond the type series. The reproduction and life history of E. baleensis are unknown but it has been postulated to lay terrestrial eggs that possibly develop directly without a tadpole stage (Largen, Reference Largen1991). The presence of E. baleensis and its endemicity have been overlooked by at least some important works on the Bale Mountains (e.g. Miehe & Miehe, Reference Miehe and Miehe1994). It has been categorized as Endangered on the IUCN Red List since the first Global Amphibian Assessment in 2004 (Stuart et al., Reference Stuart, Hoffman, Chanson, Cox, Berridge, Ramani and Young2008; IUCN, 2010).
B. hillmani (Plate 1d) was described in 1989 from specimens collected in 1986 from a single locality (Tulla Negesso). To the best of our knowledge no subsequent collections had been made, nor any reports published for any other locality (e.g. Largen & Spawls, Reference Largen and Spawls2010). The types were collected from beneath logs and boulders within giant Erica forest 50 m below the timber line on the Harenna escarpment (Largen & Drewes, Reference Largen and Drewes1989). The presence of B. hillmani and its endemicity were overlooked by at least some important works on the Bale Mountains (e.g. Miehe & Miehe, Reference Miehe and Miehe1994). The breeding biology and life history of B. hillmani are unknown but it is predicted to have terrestrial eggs with direct development (Largen & Drewes, Reference Largen and Drewes1989; Müller et al., Reference Müller, Loader, Ngalason, Howell and Gower2007). It has been categorized as Endangered on the IUCN Red List since the first Global Amphibian Assessment in 2004 (Stuart et al., Reference Stuart, Hoffman, Chanson, Cox, Berridge, Ramani and Young2008; IUCN, 2010).
Methods
We evaluated data on the change in abundance of the four endemic genera, combining information from five previous field visits (1971–1986) with that from seven teams that conducted amphibian and reptile survey fieldwork on 10 subsequent occasions (1994–2009). All six expeditions that took place this century included the four focal species as specific targets, and the teams were equipped with detailed historical locality information for these taxa. Fieldwork took place by day and night, employing visual and audio encounter surveys. Searching included netting of streams and ponds, inspecting trees and shrubs, digging leaf litter and surface soil, rolling logs and rocks, raking leaf litter, and searching through ground vegetation by hand, including some intensive searches in 25 m2 quadrats. Particular effort was applied along the edge of water bodies. Details of the field effort undertaken and frogs encountered are provided in Appendix 2. All teams recorded numbers of individuals of the four endemic frog genera. Teams 11–14 recorded search effort (as number of person hours searching) while in the field. Search effort data for the other teams, including expeditions between 1971 and 1999, were compiled retrospectively from the field notebooks of expedition members. Frogs other than the four focal species were noted but precise numbers of individuals encountered were generally not recorded.
Field data were converted into numbers of frogs encountered per person hour of searching. These data were grouped into eight localities (Fig. 1): (A) North of Sanetti (2,800–3,900 m), mostly around Dinsho and south of Goba up to the northern edge of the Sanetti Plateau, (B) Sanetti Plateau (c. 3,800–4,150 m), (C) Tulla Negesso and areas close to the road, down to the lower edge of the main centre of Rira village (2,900–3,250 m), (D) Fute and Kotinsa, superficially less disturbed (than Tulla Negesso) giant Erica forest along the Harenna escarpment east of the road (3,200–3,255 m), (E) Degebato and Galema, superficially less disturbed giant Erica forest along the Harenna escarpment west of the road (3,200–3,300 m), (F) In the vicinity of the WWF hut below Rira, down to the lower rim of the Rira basin (2,700–2,850 m) but close to the road, (G) in and immediately around the Katcha clearing (c. 2,350–2,450 m), and (H) around the Shawe River bridge and areas close to the road south of here, including the marshy clearing at Magano (c. 1,700–1,950 m).
Likelihood of site-level extinction of frogs was assessed with optimal linear estimation (Cooke, Reference Cooke1980; Solow, Reference Solow2005), a non-parametric method that allows extinction date to be estimated based on the distribution of most recent sightings. We applied the technique reported by Solow (Reference Solow2005) to generate an estimate of extinction date, with 95% confidence limits (see Appendix 3 for full details). Change in numbers of individuals over time was assessed by fitting models in a generalized additive modelling (GAM) framework. We used GAM to model sightings as a function of effort trend as a smooth, non-linear function of time, and to provide a framework for testing the statistical significance of changes. GAM is advantageous in long-term trend analyses because it allows change in mean abundance to follow any smooth curve, not only linear forms (Fewster et al., Reference Fewster, Buckland, Siriwardena, Baillie and Wilson2000). Calculations were carried out using the MGCV package (Wood, Reference Wood2006) in R v. 2.11 (R Development Core Team, 2010).
Results
Raw encounter data are reported in Appendix 2 and summarized in Table 1. A single S. osgoodi (identified from a photograph provided by M. Hoffman) was found at Katcha on 14 October 2003 but we were aware of this visit and find only after our study had been completed and so it is not included in our quantitative analyses. S. Spawls possibly found three S. osgoodi in a clearing 3 km south of Rira (January 1995) but their identity has not been confirmed (possibly Altiphrynoides instead). No specimens were found by later expeditions during substantial fieldwork, so that to the best of our knowledge S. osgoodi has not been collected since 1986, perhaps observed only twice since then, and not observed since 2003 despite concerted attempts to locate specimens. From the quantitative data, Cooke's estimator gives an estimated date of extirpation of S. osgoodi from the sampled region of 2016 but the confidence interval, CI, is wide (95% CI 1999–2781; 80% CI 2003–2100). The encounter rate data are too non-linear to use simple regression to test for significant decline but a GAM using sightings pooled across study sites showed a good fit, illustrating significant decline since the mid 1970s (t = 2.95, P > 0.05; Fig. 2a).
Fig. 2 Quantitative decline of frogs in the Bale Mountains (Fig. 1), shown as generalized additive modelling trends (lines) fitted to abundance (as sightings per person hour of searching; Table 1) data for focal species of frogs: (a) Spinophrynoides osgoodi 1971–2009, (b) Altiphrynoides malcolmi 1971–2009, (c) Balebrevicpes hillmani 1986–2009, and (d) these three species plus Ericabatrachus baleensis 1971–2009.
Table 1 Numbers (and individuals per hour in parentheses) of the four species of frogs surveyed in the Bale Mountains across eight localities (A–H; see Methods for further details and Fig. 1) during 15 numbered field trips between 1971 and 2009.
* Also part of locality (C) and is the type locality of E. baleensis and B. hillmani.
More than 100 A. malcolmi were recorded in four visits during 1994–1999, most on the Harenna escarpment but also on the north-east edge of the Sanetti Plateau. A further 25 were found in six subsequent visits (2006–2009), all but one on the Harenna escarpment. Together these specimens extend the altitudinal range of the species to c. 2,500–4,000 m (from 3,200–4,000 m, Largen, Reference Largen2001). The Harenna specimens were found during the day, almost all under logs, and some (including all from the north-east edge of Sanetti) under rocks. Analysis of encounter data with GAM showed a significant decline in abundance using sightings pooled across study sites (t = 3.25, P < 0.05; Fig. 2b).
Only three E. baleensis were found by the 10 expeditions post-1986 (1994–2009), and all of these in relatively undisturbed habitat east of the type locality. Despite dedicated searches no specimens have been found at the type locality or at Katcha since their original discovery. Statistical analysis is not appropriate for the patchy quantitative data but E. baleensis is probably extirpated or rare at the type locality. Comparison of the stream at the type locality at the time of discovery (1986) and the recent expeditions (2006–2009) reveals substantial habitat alteration (Plate 2). The stream is no longer a swift mountain torrent (Largen, Reference Largen1991) but is now a broad, boggy, muddy and relatively slow-flowing waterway heavily trampled by domesticated cattle. The stream is also now used by local people to wash clothes, with one section diverted to form a leat that serves the nearby dwelling. This habitat change happened between 1999 and 2006.
Plate 2 Habitat degradation in the Harenna Forest, Bale Mountains (Fig. 1): (a) stream trampled by cattle in Erica forest at the type locality (Tulla Negesso) of Balebreviceps and Ericabatrachus, September 2006, (b) livestock trails, cut wood and lack of ground cover in Erica forest between Tulla Negesso and Fute, December 2010, (c) collection site of Balebreviceps under rotten wood forming part of old livestock fence (new bamboo fence in background) in heavily grazed clearance just below Rira, December 2010, and (d) house and bamboo fencing in man-made clearance in Erica forest, Fute, June 2009.
Six specimens of B. hillmani have been found at the type locality since the original collection in 1986. Only three of these were found in the six visits since 2006, despite considerable effort. Comparison of the type locality giant Erica forest in 1986 and 2006–2009 demonstrates substantial change (Plate 2). There is now a greatly reduced leaf litter, fewer trees, an almost compete absence of logs (removed for firewood and fencing), a human settlement on the edge of the forest, and an introduction of cows and other livestock that has resulted in the forest floor being heavily grazed, trampled and crossed by muddy tracks. At least two of the recent B. hillmani from the type locality were found under piles of rotting epiphytic moss that had probably been stripped from trees during firewood collection. In contrast 18 B. hillmani were encountered (2008–2009) at a much higher rate in much less disturbed Erica forest a short distance east of the type locality. Here specimens were found under logs and in live moss, much as described for the type series (Largen & Drewes, Reference Largen and Drewes1989). Seven additional specimens were found under dead wood on the lower edge of Rira, in open grassy habitat close to the road. The latter specimens extend the lower altitudinal range of the species to 2,815 m, and are the first record of the species outside Erica forest. People in Rira reported that B. hillmani are also found among dead Hagenia/Schefflera wood used to build fences to restrict livestock close to Rira. The best-fit GAM for the pooled Tulla Negesso + Rira data suggests a significant attenuating decline (t = 4.41, P < 0.01; Fig. 2c).
Grouping encounter data for all four endemic genera across all sites and times demonstrates a significant decline, with a best-fit linear model (t = 3.14, P > 0.05; Fig. 2d). All expeditions found several other species of frogs, on both the northern and southern slopes below the Sanetti Plateau (Appendix 2). These were Ptychadena (c. four species), Leptopelis (three or four species), Bufo sp., Xenopus sp., Phrynobatrachus sp., Hyperolius sp., Afrixalus sp. and Paracassina kounhiensis. In particular Leptopelis and Ptychadena were common and frequently abundant near water bodies, even at very disturbed sites in and close to Rira. Large tadpoles, probably of L. gramineus, were found at up to c. 4,000 m on the edge of the Sanetti Plateau. Seventy-two frogs of 11 species were swabbed in 2008 and 2009, and 42% (including the three focal species encountered) tested positive for the chytrid fungus Batrachochytrium dendrobatidis (Gower et al., Reference Gower, Doherty-Bone, Aberra, Mengistu, Schwaller and Menegon2012).
Discussion
B. hillmani and E. baleensis have declined substantially at their joint type locality (Tulla Negesso) in association with substantial human-induced habitat degradation. The presence of B. hillmani in greater numbers (and three E. baleensis) in more pristine habitat, similar to that found at Tulla Negesso 25 years ago, supports the interpretation that habitat degradation is probably the major cause of population declines at Tulla Negesso. The occurrence of B. hillmani under dead wood in Rira indicates that the species can survive in suitable microhabitats in disturbed areas. E. baleensis has been found only in close association with undisturbed streams and probably has a narrower range of potentially suitable habitat than B. hillmani in the changing Harenna landscape. Local people reported to the 2006–2009 field teams an increased irregularity in seasonal climate patterns but it is difficult to assess the possible impact of this upon frog populations given that our data are from sites that have undergone rapid habitat change. More work is needed if the impact of future expected climate change is to be understood.
S. osgoodi has declined greatly in the Bale Mountains to the extent that although previously considered to be ‘particularly common in the Bale Mountains National Park’ (Largen & Spawls, Reference Largen and Spawls2010; see also IUCN, 2010), its continued existence is not yet established. The abundance of A. malcolmi has also decreased significantly. Given our evidence, the IUCN Red List categories of these four species should be reassessed. The current IUCN assessments include statements about abundance and threat that are now known to be incorrect. Although B. dendrobatidis was recorded no dead or moribund frogs were found, and it remains to be seen to what extent this pathogen is implicated in the declines. Although B. dendrobatidis is known to kill frogs elsewhere it has been associated with the decline of only a single species of African frog, Nectophrynoides asperginus in Tanzania, and even then habitat deterioration was also implicated (Weldon & du Preez, Reference Weldon and du Preez2004; Channing et al., Reference Channing, Finlow-Bates, Haarklau and Hawkes2006).
The Bale Mountains National Park is facing major challenges (Frankfurt Zoological Society, 2007), caused chiefly by the rapidly growing human population. Even within the short period of 2006–2009 the negative impact of humans on the ecosystems of the Park was apparent, with deforestation at Harenna and increasing effects of livestock. Given that most conservation in the Bale Mountains has hitherto focused on large mammals (as elsewhere in Ethiopia, Loader et al., Reference Loader, Mengistu, Schwaller, Gower, Nagel and Getahun2009), the threats to Bale ecosystems more generally have been under appreciated. The continued presence of endemic mammals and patches of, for example, giant Erica, could lead to the superficial conclusion that Bale forests are relatively stable but our examination of a smaller faunal element, the frogs, presents a different perspective.
We suggest several priority research objectives for the Bale amphibian fauna. More intensive and temporally and spatially broader searches for S. osgoodi are required, with hunts for breeding aggregations such as those described by Grandison (Reference Grandison1978) perhaps the best target. More surveys are required to complete an inventory of the amphibians, with surveys away from roads and in more pristine habitat as well as in degraded ecosystems; these surveys should include areas surrounding the National Park. More basic ecological data on frogs need to be gathered, especially on the reproductive biology of B. hillmani and E. baleensis. More surveys are required across a range of localities and habitats to determine where monitoring efforts could best be focused. Research on other Bale organisms is required, with the works of Miehe & Miehe (Reference Miehe and Miehe1993, Reference Miehe and Miehe1994), studies of endemic mammals (see Introduction) and the Bale Mountains National Park General Management Plan (Frankfurt Zoological Society, 2007) providing a framework with which this can be integrated.
In terms of conservation management the growing numbers and destructive activities of people living within the National Park need to be addressed. When the Park is formally gazetted all settlement will be illegal but until then their status remains a grey area. Protection of key habitats is an immediate priority until human disturbance is halted across the Park. Human population growth in Ethiopia is high (Largen & Spawls, Reference Largen and Spawls2010; UN, Department of Economic and Social Affairs, Population Division, 2011), and this is reflected in the increase in people living within the Park from 2,500 in 1986 (Hillman, Reference Hillman1986) to > 40,000 in 2003 (Frankfurt Zoological Society, 2007). The Erica forests of the Bale Mountains have been limited historically by fire and grazing (Miehe & Miehe, Reference Miehe and Miehe1993, 1994) but more active deforestation is now taking place, extended grazing and wood collecting are altering the forest floor, and regeneration of these forests remains poorly understood. The importance of working properly with local people in conservation management in Africa has been recognized (Abrams et al., Reference Abrams, Anwana, Ormsby, Dovie, Ajagbe and Abrams2009) but we believe that within the Bale Mountains National Park the right balance has not yet been reached. The General Management Plan (Frankfurt Zoological Society, 2007) already recognizes much of what we conclude here but our data for endemic frogs emphasizes the urgency of conducting further biological research and developing appropriate conservation management in the region.
Acknowledgements
For advice, help with fieldwork, and permits for research and export, we thank (in no particular order) Hailu Tadesse, Kifle Argaw, Yeneneh Teka, Daniel Pawlos and Birutesfa Yimer (Ethiopian Wildlife Conservation Authority), Afework Bekele and Abebe Getahun (Addis Ababa University), Isa (WWF), Daniel Tilaye (Bale Mountains National Park), Ryan Kerney (Harvard University), Alastair Nelson, Anouska Kinahan and Thadaigh Baggallay (Frankfurt Zoological Society), Michael Geiser (University of Basel), Zelealem Tefera, Addis Berhanu, Sisay Shewamene, Red Jackal Tour Operators, the people of Rira, Colin Tilbury, Bill Branch, Chris Smith, Jon Gower, Alexia Kerney, Jonathan and Tim Spawls, and our guides in 2008–2009 (Issa, Ahmed, Hussein, Hussein and Mohammed). The Harvard University expedition received funding from the Museum of Comparative Zoology's Putnam Expedition Grants. Fieldwork in 2008 and 2009 was supported in part by a National Geographic Expedition Grant (CRE Grant #8532–08). The following bodies also funded surveys and laboratory work: Ethiopian Wildlife Conservation Authority, University of Basel, European Union Synthesys project (AAM), The Natural History Museum London (DJG, SPL), University of Richmond Faculty Research Committee (RdS), and Stipendienkommission für Nachwuchskräfte aus Entwicklungsländern, Basel (AAM).
Appendices 1–3
The appendices for this article are available online at http://journals.cambridge.org
Biographical sketches
David Gower is a herpetologist specializing in systematics and evolution. Roman Aberra works in Ethiopian conservation, with a special interest in frogs. Silvia Schwaller conducted her Masters thesis on environmental change in the Harenna Forest. Malcolm Largen is a leading authority on herpetology in Ethiopia. Ben Collen is a conservation biologist with expertise in quantitative analysis. Steven Spawls is an expert in East African herpetology. Michele Menegon researches the diversity and evolution of East African amphibians and reptiles. Breda Zimkus is a herpetologist with expertise in African frogs. Rafael de Sá is an amphibian biologist with expertise in tadpole biology. Abebe Mengistu has expertise with Ethiopian fish and frogs. Fikirte Gebresenbet is a conservation biologist working in her native Ethiopia. Robin Moore is an amphibian conservation biologist. Samy Saber is an expert on the ecology of African amphibians and reptiles. Simon Loader studies African (especially Afromontane) amphibian systematics and evolution.
