The global spread of amphibian chytrid fungus (Batrachochytrium dendrobatidis, Bd) is associated with amphibian mass mortality, population decline, and extinction. Over the past decade, concern has been expressed for the potential introduction of Bd to Madagascar, a global hotspot of amphibian biodiversity. Following years without detection, widespread Bd presence in Madagascar has now been reported (Bletz et al. 2015a), raising international conservation concern. Before reacting to this finding with a significant management response, the accuracy and context of the data warrant cautious review. Re-examination of a 10-year dataset together with results from more recent surveillance (Kolby et al. 2015) does not yet demonstrate widespread Bd presence. Detection of Bd at “positive” locations in Madagascar has been inconsistent for unknown reasons. Whether Bd is established in Madagascar (i.e. populations are self-sustaining) or instead requires continued introduction to persist also remains uncertain. The deployment of emergency conservation rescue initiatives is expected to target areas where the distribution of Bd and the risk of chytridiomycosis endangering amphibians is believed to overlap. Thus, erroneous description of Bd presence would misdirect limited conservation resources. Standardized surveillance and confirmatory surveys are now imperative to reliably characterize the distribution, potential spread, virulence and overall risk of Bd to amphibians in Madagascar.
Citation: Kolby JE, Skerratt LF (2015) Amphibian Chytrid Fungus in Madagascar neither Shows Widespread Presence nor Signs of Certain Establishment. PLoS ONE 10(10): e0139172. doi:10.1371/journal.pone.0139172
Editor: Jacob Lawrence Kerby, University of South Dakota, UNITED STATES
Received: June 30, 2015; Accepted: September 8, 2015; Published: October 14, 2015
Copyright: © 2015 Kolby, Skerratt. This is an open access article distributed under the terms of the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original author and source are credited
Funding: JEK is supported by a James Cook University Australian Postgraduate Research Scholarship. The funders had no role in study design, data collection and analysis, decision to publish, or preparation of the manuscript.
Competing interests: The authors declare that they are the original authors of http://journals.plos.org/plosone/article?id=10.1371/journal.pone.0125330.
Two recent papers provide conflicting results on whether the globally emerging amphibian chytrid fungus Batrachochytrium dendrobatidis (Bd) is now widespread and established (self-sustaining populations) in Madagascar [1,2]. Presence of Bd has been linked to a growing number of disease-driven amphibian mortality events and population declines since its discovery [3,4]. The global origin of Bd, timeline of first emergence, and reason for contemporary lethality are still unknown, although it has been present for thousands of years . Despite its historic occupation in some areas and continued spread to others, certain regions appear to have remained free of Bd and disease-associated amphibian decline until only very recently, most notably Madagascar—a global hotspot of amphibian biodiversity.
A series of proactive Bd surveillance efforts performed prior to 2010 found the pathogen to be absent in Madagascar (0% estimated prevalence with high confidence) [6–8]. Assuming Bd absence based on these data and considering the threat of introduction, the Madagascar Chytrid Emergency Cell was established in 2010 along with the development of the National Monitoring Plan to administer biannual surveys for Bd presence, performed at eight nationally distributed locations to facilitate early detection and a rapid response . Soon thereafter, a first call to arms was raised when amphibians collected from the wild in Madagascar and exported to the USA pet trade in Feb 2012 tested positive for Bd, suggesting presence and potentially recent introduction to Madagascar , as no other detections had previously been confirmed.
Nearly three years later, Bletz et al.  now report widespread Bd presence in wild amphibian communities in Madagascar. Surveillance efforts described by Bletz et al.  span nearly a decade (2005–2014), involved the sampling of 4,155 amphibians, and were performed at 52 survey sites across the country. Bd was detected at 10 sites, from five locations (i.e. multiple sites tested positive at some locations, e.g. two separate Bd-positive stream sites within a national park). Infection prevalence reported from these sites was generally low, but reached up to 100% on occasion. Accordingly, this announcement of seemingly sudden widespread Bd distribution together with unpredictable high prevalence of infection ignited considerable alarm among the conservation community, as it suggests that catastrophic disease-associated decline in Malagasy amphibian biodiversity is now immediately possible.
One month following the final Bd-positive survey described by Bletz et al.  from Jan 2014, a highly intensive national surveillance program did not detect Bd presence in samples collected at 47 survey sites distributed throughout the country . This sampling effort included 508 amphibians swabbed for Bd and 68 Bd eDNA water filter samples processed to detect the pathogen in amphibian habitats. Locations surveyed by Kolby et al.  included 3/5 Bd-positive regions described by Bletz et al. . Although Bletz et al. suggested Bd detection is greater in the cooler dry season, this pathogen has also been detected in Madagascar during the warmer wet season and our lack of detection at “positive” locations is curious, especially since our methods incorporated multiple techniques to increase sensitivity and power of detection. Thus, field survey results presented by Kolby et al.  strongly conflict with the assertion that Bd is widely distributed in Madagascar.
Before significant conservation management decisions are developed based on the distribution of Bd described by Bletz et al. , it is important to consider and resolve the disparity in results provided by Kolby et al. . Three main plausible explanations spring to mind: 1. the studies varied significantly in diagnostic sensitivity and specificity, 2. the amphibian chytrid fungus detected by PCR by Bletz et al.  and Kolby et al.  behaves differently to the Bd detected elsewhere in the world, and 3. non-Bd material is reacting with Bd primers and falsely suggesting its presence in Madagascar. Bletz et al.  partially addressed the latter hypothesis by conducting a lineage-specific PCR that suggested some of the positive samples were molecularly similar to the global pandemic Bd lineage, but histological confirmation of infection with Bd in Malagasy amphibians still does not yet exist. In considering hypothesis 1, variation in accuracy, as a possible explanation for the discordance among survey results, amphibian sampling efforts performed from 2005–2014 demonstrated an overall lack of standardization in survey design, including: the selection of locations sampled, sample collection and storage methods, and laboratory diagnostic techniques. Accuracy of the qPCR test for Bd detection has been shown to vary according to both field sampling and laboratory diagnostic methods  and Bletz et al.  further demonstrate that employing different DNA extraction methods will affect the detection of Bd from skin swabs. Given the aforementioned variation in field protocols and laboratory techniques, each study has introduced additional unique variation in diagnostic sensitivity and specificity over the 10 years of surveys. Thus, some unknown cumulative degree of uncertainty is now embedded within the description of the current presence and distribution of Bd in Madagascar.
Two anomalies in the data specifically deserve attention: inconsistent detection at sites reported as Bd-positive and dramatic fluctuation in measured Bd prevalence. Detection of Bd at specific survey sites was infrequently followed by subsequent detection (Table 1). For example, Bd was last detected at Makay and Ankarafantsika 3–4 yrs ago, in 2011 and 2012, respectively, and recent confirmatory survey efforts at both sites produced only negative results. If these data reflect true Bd absence following earlier detections, then it is plausible that Bd failed to become established at these locations and develop self-sustaining populations. These observations now introduce uncertainty regarding the current presence of Bd at most sites in Madagascar reported as “Bd-positive”. This is because 8/10 of these sites were classified as “Bd-positive” based on single detection events (Table 2), where the assumption of Bd establishment may likewise be spurious. This sporadic pattern of Bd detection also raises question as to the manner in which Bd survey results are commonly communicated; do sites of Bd detection followed only by lack of detection warrant a "Bd-positive" label and permanent loss of freedom of disease status? The World Organisation for Animal Health (OIE) Aquatic Animal Health Code (Chapter 8.1: Infection with Batrachochytrium dendrobatidis) states that a country where Bd has been detected can be reclassified as “free from infection with B. dendrobatidis” if targeted surveillance has been in place for at least two consecutive years without detection . If this approach was to be applied at the field site level within Madagascar, and elsewhere, it would substantially change the manner in which researchers populate Bd distribution maps—at present, even a single Bd-positive record is frequently used to symbolize Bd persistence at that location, with or without subsequent surveillance.
Bletz et al.  mention that their long-term methodological inconsistencies place a limitation on data interpretation and,"… may confound time and season with detection method and could in part compromise the conclusions of the recent detection of Bd and seasonality trends." The exceptionally high Bd prevalence of 100% inferred from material collected at Ankaratra (site: Tavolotara) in Aug 2013, was both preceded and followed by complete lack of detections in Feb 2013, Dec 2013, and March 2014. Environmental conditions measured during the most recent survey at Ankaratra in March 2014 were favorable for Bd to thrive, with daytime air and water temperatures ranging from 12.4–15.9 C and 13.4–15.2 C, respectively. Bd mortality (i.e. death of the pathogen) does not normally occur until temperatures rise to 28 C and above , and even following death for any reason, its molecular presence will persist and extend detectability. In an aquatic habitat, Bd is likely to remain detectable year-round despite sometimes variable abundance, as has been observed in long-term water filtration surveys at affected wetlands . Although the Bd in Madagascar might behave dramatically unlike that studied elsewhere, no evidence yet supports this hypothesis apart from variation in virulence observed among lineages . Bletz et al.  hypothesize that this phenomenon at Ankaratra may be explained by a seasonal variation in Bd abundance caused by some unidentified factor and/or there was a changeover in the strain of Bd present (similar to hypothesis 2, above). Considering all available information, the law of parsimony instead suggests that samples from Aug 2013 were more likely compromised and involved some form of field or laboratory error (hypothesis 1).
In order to reduce aforementioned uncertainties, current and future Bd surveillance methods must be standardized to prevent continued challenges in field data interpretation and potential loss of conservation value produced by these efforts. Moving forward, variation in detection that may confound observed patterns of Bd presence can be minimized by establishing longer-term surveys at suspected Bd-positive sites and ensuring that samples are collected, stored, and analyzed following standardized established methods for Bd. Multiple complementary Bd sample collection and diagnostic techniques can also be incorporated into future surveys to increase the confidence of results, e.g. collection of water samples for eDNA analysis at aquatic habitats where amphibian are simultaneously swabbed for Bd , and histological confirmation of Bd presence in an amphibian that tests positive by skin swab . Water filtration can capture Bd particles shed from a host [15,18,19] and if detected, corroborate swab-based "Bd- positive" site characterizations in a highly cost-efficient manner. At the time of writing (August 2015), histological evidence of Bd infection in wild Malagasy amphibians still does not exist; such data would help prove that Bd presence is certainly causing the PCR-based detections and help rule out hypotheses 1 and 3, above. Further, fungal isolation should be performed and results verified by an OIE reference laboratory .
In conclusion, the uncertain distribution and potential impact of Bd presence in Madagascar requires additional investigation before accurate evaluations can be made. Standardized field surveillance methods and laboratory diagnostic techniques are needed to more carefully investigate the presence of Bd both at sites where it has and has not yet been detected. The former is necessary to build longer-term surveys that can assess whether or not Bd is established in Madagascar and the latter to monitor future Bd spread into potentially Bd-negative locations. These data can then be combined with those provided by Bletz et al.  and Kolby et al.  to more confidently assert whether Bd is truly present and widespread, especially in the absence of any obvious sign of disease. Still, many amphibian species in Madagascar have not been monitored in a long-term standardized fashion, and thus any Bd-associated decline may be occurring unnoticed. Therefore, population monitoring of key species likely to be affected warrants urgent establishment. The application of skeletochronology  and/or intensive mark-recapture surveys may shed light on survival patterns in amphibian communities where Bd has been identified or is suspected. The presence, distribution, virulence to native species and clade membership of Bd in Madagascar must be verified before its potential impact on Malagasy amphibians can be accurately predicted.
Conceived and designed the experiments: JEK. Performed the experiments: JEK. Analyzed the data: JEK LFS. Wrote the paper: JEK LFS.
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