Widespread population declines in terrestrial Plethodon salamanders occurred by the 1980s throughout the Appalachian Mountains, the center of global salamander diversity, with no evident recovery. We tested the hypothesis that the historic introduction and spread of the pathogenic fungus Batrachochytrium dendrobatidis (Bd) into the eastern US was followed by Plethodon population declines. We expected to detect elevated prevalence of Bd prior to population declines as observed for Central American plethodontids. We tested 1,498 Plethodon salamanders of 12 species (892 museum specimens, 606 wild individuals) for the presence of Bd, and tested 94 of those for Batrachochytrium salamandrivorans (Bs) and for ranavirus. Field samples were collected in 2011 from 48 field sites across a 767 km transect. Historic samples from museum specimens were collected at five sites with the greatest number and longest duration of collection (1957–987), four of which were sampled in the field in 2011. None of the museum specimens were positive for Bd, but four P. cinereus from field surveys were positive. The overall Bd prevalence from 1957–2011 for 12 Plethodon species sampled across a 757 km transect was 0.2% (95% CI 0.1–0.7%). All 94 samples were negative for Bs and ranavirus. We conclude that known amphibian pathogens are unlikely causes for declines in these Plethodon populations. Furthermore, these exceptionally low levels of Bd, in a region known to harbor Bd, may indicate that Plethodon specific traits limit Bd infection.
Citation: Muletz C, Caruso NM, Fleischer RC, McDiarmid RW, Lips KR (2014) Unexpected Rarity of the Pathogen Batrachochytrium dendrobatidis in Appalachian Plethodon Salamanders: 1957–2011. PLoS ONE 9(8): e103728. https://doi.org/10.1371/journal.pone.0103728
Editor: Jason E. Stajich, University of California-Riverside, United States of America
Received: April 2, 2014; Accepted: July 5, 2014; Published: August 1, 2014
This is an open-access article, free of all copyright, and may be freely reproduced, distributed, transmitted, modified, built upon, or otherwise used by anyone for any lawful purpose. The work is made available under the Creative Commons CC0 public domain dedication.
Data Availability: The authors confirm that all data underlying the findings are fully available without restriction. All relevant data are within the paper and its Supporting Information files.
Funding: The National Science Foundation (http://www.nsf.gov/) provided support to KRL (DEB 0917653, 0213851, 0234386). Funding for this project was provided by the University of Maryland and Smithsonian Seed Grant Program (http://www.sgsi.umd.edu/) to KRL, RCF and RWM. The funders had no role in study design, data collection and analysis, decision to publish, or preparation of the manuscript.
Competing interests: The authors have declared that no competing interests exist.
Globally, amphibians have experienced population declines and extinctions ,  with many recent population declines (e.g., , ) caused by Batrachochytrium dendrobatidis (Bd), a pathogenic fungus that causes chytridiomycosis . Population declines of Central American plethodontid salamanders were documented  in the late 1970s to early 1980s by pairing field surveys with historic field notes and museum records; subsequent molecular analysis of these museum specimens  demonstrated that Bd was the likely driver of these declines.
The causes for many amphibian population declines remain enigmatic. For instance, in the eastern US – the center of global salamander diversity – Highton  described widespread declines in abundance in 180 of 205 populations of 38 Plethodon salamander species by the early 1980s, but he was unable to attribute a cause to most of the declines. Contemporary re-surveys of 72 of Highton's populations in Great Smoky Mountain National Park identified reduced occupancy and reduced abundance in 28 populations of six Plethodon taxa, yet Bd was not detected in any of the 485 Plethodon tested .
In this study, we tested the hypothesis that the disease chytridiomycosis, caused by Bd infection, was the driver of Appalachian Plethodon salamander declines reported in the 1980s. While the Great Smoky Mountain NP study  covered a wide range of elevations, it was restricted to contemporary field surveys of 35 sites in the Southern Appalachians. If Bd were responsible for the population declines in Appalachian Plethodon, we expected to detect an increase in prevalence of Bd in museum specimens collected prior to the reported declines in the 1970s as reported for Central American plethodontids . To test this hypothesis we extended our surveys for Bd in both time and space. We sampled museum specimens collected by Highton and colleagues from 1957–1987 at five sites  and conducted field resurveys of 79 historic sites in 2011. We tested a subset of these samples for the newly describe salamander chytrid, Batrachochytrium salamandivorans  and for ranavirus .
We worked with staff at the National Museum of Natural History to determine which historic collecting sites had the most extensive records to determine contemporary resurvey sites. From June–October 2011 we sampled all species of salamanders at 79 historic collecting sites originally visited by R. Highton and colleagues. At all sites we captured salamanders from 3, 50×3 m diurnal cover object plots where we turned over every log, rock or branch and captured all salamanders encountered. At some sites we also captured salamanders from 2, 50 m nocturnal visual encounter surveys where we captured every salamander seen along the transect. We identified each capture to species and sex, and measured snout-vent-length (SVL), mass, and body temperature. We swabbed each salamander 5 times on each limb and on the venter, and stored the swab in a 2 ml tubes with 70% ethanol. We used a new bag for each animal and changed gloves between captures to minimize the possibility of cross contamination, which also eliminated the need for disinfecting calipers. We accessed sites along well-traveled roads and hiking trails that were relatively dry, minimizing the need for disinfection.
To minimize cost of molecular analyses, we planned to establish Bd prevalence in the field by first testing all samples of the P. cinereus and P. glutinosus species groups. We focused on these groups because of their broad ranges, abundance in museum collections, and because we had noticed species-specific differences in the degree of decline in these two groups (unpublished data). We minimized sampling from the Great Smoky Mountain NP given our prior Bd surveys in this region . Depending on the results of this first pass we planned additional sampling of other species and sites. To determine sampling effort necessary to detect Bd, we calculated the probability of detecting a false negative based on 5% infection prevalence, ,  and we attempted to sample sufficient numbers per site or species to reach that level.
In total, we tested samples from 48 of the 79 sites. The 48 sites were selected because Plethodon species still occurred there and because most of these sites had not already been sampled in 2009 . The 48 sites spanned a geographical range of 767 km and an elevational range of 401–1,687 m (Figure 1) and were located within 5 protected areas across four states: Great Smoky Mountains National Park, TN and NC (8 sites), Nantahala National Forest, NC (4 sites), Pisgah National Forest, NC (9 sites), George Washington and Thomas Jefferson National Forests, VA (25 sites) and Catoctin Mountain Park, MD (2 sites).
We worked with staff at the National Museum of Natural History to determine which specimens were available from each site to search for Bd in historic samples (Table S2). We selected five sites that had at least 100 Plethodon museum specimens collected prior to and during population declines reported in the 1980s . Four of these sites were visited during field surveys in 2011: Dismal Creek, VA, Rust – Iron Mountain, VA, Indian Grave Gap, NC, and White Oak Sinks, TN. The fifth site, Hawksbill Mountain, VA had extensive museum holdings, but we were unable to sample in the field because of the presence of an endangered species (P. shenandoah).
To minimize cost of molecular analyses, we developed a plan for testing samples that would allow us to identify the location of the oldest Bd+ sample from museum holdings and determine any geographic spread by sampling out in time and space from that location. We started by sampling specimens of the P. cinereus and P.glutinosus species groups collected at Hawksbill Mountain (1957–1979, n = 365) and Indian Grave Gap, VA (1970–1987, n = 339), because these sites had the most extensive holdings, some of the oldest collections and together covered most of our spatial and temporal focus. We expected to find Bd+ animals prior to population declines in the 1980s and began by sampling roughly 60 specimens per species group per decade. Depending on what we found at these two sites, we planned similar sampling effort for specimens collected during the 1970s at the remaining three sites (Dismal Creek, VA: 1969–1974, n = 96, Rust – Iron Mountain, VA: 1972–1987, n = 61, and White Oak Sinks, TN: 1971–1974, n = 31), to establish the date and location of the oldest record and any potential geographic spread. To determine sampling effort necessary to detect Bd, we calculated the probability of detecting a false negative based on 5% infection prevalence , , and we ended sampling when we had sufficient numbers per site or species to reach that level.
We followed established methods ,  to collect swabs from preserved specimens from the two species groups (Table S1). To decrease chances of contamination from errant pieces of skin or zoospores floating in the jar, we rinsed each salamander with 70% ethanol before swabbing, and held each specimen in a new plastic bag to minimize cross contamination from handling. We also collected swabs of the alcohol in each preservation jar to determine if that might be a source of contamination.
DNA Extraction and PCR
We extracted DNA from the 2011 field swabs following the Qiagen BioSprint manual for Tissue Extraction using a three-hour incubation in lysis buffer. Prior to extraction, we removed residual ethanol from the swabs with a speed vacuum. For museum specimen swab samples, we performed DNA extractions in an ancient DNA lab at the Center for Conservation and Evolutionary Genetics. Ancient DNA labs are free from modern DNA, which can contaminate samples . We extracted DNA from museum swabs following the Qiagen Blood and Tissue Kit 96 manual for Tissue Extraction using an overnight incubation in lysis buffer and a final elution volume of 80 ul. To verify that our DNA extraction methods could extract Bd DNA, we included known Bd positive control swabs from live and preserved frogs at the beginning and end of extracting the 2011 samples and the museum samples, respectively.
We used standard methods to quantify pathogen load using qPCR ,  with minor modifications as follows. We used iTaq supermix with Rox (Bio-Rad) and followed their qPCR reaction protocol. We ran all contemporary DNA samples individually, and we re-ran positive samples in triplicate to verify and quantify Bd load in zoospore genomic equivalents (ZGEs) using standards of 100, 10, 1, 0.1 ZGEs developed from Puerto Rican isolate, JEL 427. Because DNA degrades over time, we are unable to estimate ZGEs of museum samples so we ran these samples in duplicate to verify Bd presence. Bd positive and negative PCR controls (water) were used in each qPCR run.
To verify that our protocol successfully extracted and amplified ancient DNA, in the potential absence of amplification of Bd, we developed primers to amplify Plethodon DNA (GenBank: JF731309.1, Pleth1F 5′ TCGGACGAGGAATTTATTATGG 3′ and Pleth1R 5′ GACATATCCTATGAAAGCTGTTGC 3′). We tested 36 P. cinereus and 31 P. cylindraceus DNA extracts using SybrGreen qPCR following the iTaq SybrGreen Supermix with Rox protocol (Bio-Rad).
We sequenced 21 putative Bd positive samples (four 2011 samples, 17 museum samples) using conventional PCR to amplify Bd DNA using the ITS and 5.8S primers . We then cleaned amplified PCR products with ExoSAP-IT (United States Biochemical), and sequenced the cleaned amplicons using the BigDye Terminator Cycle Sequencing Kit (Applied Biosystems, Inc). The sequenced products were column filtered, dried down, rehydrated with 10 ul of HPLC purified formamide, and then analyzed on an Applied Biosystems 3130xl DNA Analyzer. Individual sequences were assembled and edited in Sequencher 5.1.
To test for the two other known amphibian pathogens we followed published PCR methods for Bs  and qPCR methods for ranavirus . We tested a subset of 94 field samples from the two species groups (P. cinereus = 21, P. welleri = 5, P. richmondi = 10, P. cylindraceus = 19, P. glutinosus = 31, P. yonahlosee = 8) sampled across 26 sites to maximize geographic coverage.
Statistics and Mapping
We calculated 95% confidence intervals (CIs) for our prevalence estimates for Bd, Bs and ranavirus. We used the package ‘Hmisc’  in R . We used the number of positives, the total number of individuals sampled, alpha = 0.05 (Type I error) and the Wilson score interval for the CI estimates .
We had permits from state and federal agencies for handling and swabbing live amphibians – Maryland (DNR Permit No. 50269), Virginia (VADGIF Permit No. 042151), North Carolina (Wildlife Resources Commission Permit No. 11-SC00547), Tennessee (Wildlife Resources Agency Permit No. 3636) and Great Smoky Mountains NP (Permit No. GRSM-2011-SCI-0059). We had permission from the National Museum of Natural History for sampling museum specimens. We received approval for the research from the University of Maryland Institutional Animal Care and Use Committee (R–11–11).
We surveyed 79 sites in 2011 and collected 1,436 swabs from 26 plethodontid salamander species representing Plethodon, Eurycea and Desmognathus genera. We tested 606 of those swabs for Bd from 11 species of our focal genus Plethodon (Table S1). Overall prevalence for Plethodon from 2011 field samples was 0.7% (95% CI: 0.3–1.7% prevalence; Table 1, Table 2). There were four Bd+ samples that all had low infection intensities (average zoospore genomic equivalents = 7.9, range 2.3–20.4), and were all P. cinereus sampled from the same site in Catoctin Mountain Park, MD in October 2011 (Table 2). Three of the positive samples exactly matched Bd sequences in GenBank (accession# AY598034). The fourth sample did not produce a good quality sequence, likely because of low infection intensity, but amplified four times so we considered it a true positive following Hyatt et al., . Because of low number of positives we did not test the other taxa to reduce costs.
We collected swabs from 892 museum specimens of six Plethodon species from 5 sites (Table S1). All museum specimens were negative for Bd (95% CI: 0–0.4% prevalence; Table 1, Table 2). Because we did not detect any positives at Hawksbill Mountain and Indian Grave Gap, VA we limited the number of samples at the three geographically intermediate sites to reduce cost. We tested swabs of the alcohol from 27 preservation jars for Bd, and all were negative.
We detected non-specific amplification in 23 of the samples after qPCR cycle 40, but we ruled these out as Bd when they did not re-amplify and the product sequences did not match expected Bd sequences. Sequences from nine putative Bd positive museum samples produced a 42-bp consensus sequence, excluding primers, which did not align with that of Bd or with any known sequence in GenBank. We were unable to deposit the consensus sequence in GenBank due to their requirements on minimum base pair size; it is provided here: 5′AACTAGTTATAGATGCCATGTATTGAGAATTGTGTTGCCGAA 3′. DNA extracted from the museum specimen swabs was of good quality as indicated by successfully amplification of salamander DNA from all 67 samples tested.
All of the 94 samples collected during 2011 field surveys from six Plethodon species were negative for both Bs and ranavirus, with prevalence estimates for each to be 0–4% using a 95% CI.
We found no evidence that chytridiomycosis, caused by Bd infection, was associated with historic declines of Appalachian Plethodon salamanders. Sample sizes were large enough to indicate with 95% confidence that the prevalence of Bd infection was below 2% for both our historic and contemporary samples. If we combine our dataset with all other published studies that have tested Plethodon spp. for Bd (Table 3), only 19 Plethodon salamanders out of 2,728 have tested positive for Bd (95% CI: 0.4–1.1% prevalence).
We find it unusual that these Appalachian salamanders exhibit such low incidence of Bd infection for several reasons. First, Bd has been present in the Appalachians at least since the 1970s  and most surveys for Bd across the eastern US have produced prevalence estimates of 10–40% (e.g., –). Second, in laboratory infection trials Plethodon salamanders are susceptible to Bd ,  and some die from Bd infection . Third, the environment in which Plethodon salamanders live is suitable for Bd . Finally, populations of terrestrial plethodontid salamanders from Central America have declined due to chytridiomycosis historically  and currently , .
We explain this low incidence of Bd with the following possibilities: 1) infected salamanders are not detected, 2) the Appalachians harbor a unique strain of chytrid fungus that does not amplify using these primers, and/or 3) Plethodon host traits limit Bd infection. We discuss each of these below as well as other potential causes of what remains enigmatic Appalachian Plethodon declines.
Lack of detection: If infected salamanders were present in the region, lack of detection might be explained if infected animals occupied unsampled habitats such as underground. Experimental studies have shown that when individuals of P. cinereus, P. montanus, and P. glutinosus salamanders are infected with high Bd levels >1×106 zoospores) most ndividuals sustained an infection or xperienced ortality 5 to 43 days post exposure 27–29,31,32]. Given our extensive spatial and temporal sampling efforts, in addition to sampling by others (Table 3), we consider it likely that some Bd infected salamanders would have been detected, during the time course of infection, before they moved underground.
It is also possible that our lab procedures, although highly sensitive, missed some light Bd infections (e.g., ), especially in museum specimens where DNA degrades over time and is damaged in formalin. However, it is unlikely that we missed heavy Bd infections if they were present because previous studies  reported 78.1% accuracy detecting Bd infections of >300 ZGEs using duplicate qPCR runs from 40 year old museum specimens of Central American plethodontids.
Pathogen strain: If the eastern US had an endemic strain of chytrid (e.g.,, ), especially one that did not amplify with these primers, then this might explain differences in response of plethodontid salamanders in Central America  to that of eastern plethodontids , . We have good evidence that Bd recently moved into Central America  and caused declines in plethodontid populations from Mexico through Panama , , but we have no evidence of these types of epidemics from the northeastern US. A long history of coexistence would likely be associated with low virulence of the pathogen , which may result in low infectivity. Few strains of Bd from the eastern and midwestern US have been cultured, leaving the possibility of an undescribed endemic strain in the region of our surveys.
Host Traits: Host defenses such as production of antimicrobial peptides , antibiosis by resident skin bacteria , , or genetic defenses  may contribute to low Bd infection prevalence. The only evidence for such host defenses in Appalachian populations is from P. cinereus in which the presence of certain antifungal bacteria can reduce Bd infections in the lab  likely through the production of toxic metabolites . However, there has been no systematic survey of the geographic or taxonomic distribution of these innate and adaptive immune responses.
Alternative causes: If Bd did not cause these declines, then what other factors might cause such synchronous population declines in so many species and populations across the eastern US ? Previous studies from our lab ,  have provided evidence that over-collecting, deforestation, and other anthropogenic factors were not involved and suggested that both disease and climate change are potential causes of these population declines .
A novel pathogen may be responsible for these Plethodon population declines. While our samples for Batrachochytrium salamandrivorans (Bs) and ranavirus were all negative, they were limited in number and only field samples were tested, leaving open the possibility that they were more prevalent historically. Bs is a recently discovered Batrachochytrium species associated with mortality in the fire salamander Salamandra salamandra in the Netherlands  that to date, has not been detected in the US. Ranavirus is widely distributed in the eastern US and has been associated with mass mortalities of aquatic-breeding amphibians . Ranavirus has been detected at 80%, in salamander Great Smoky Mountains NP salamanders, primarily in aquatic species of Desmognathus . Future studies should examine historical samples for the presence of Bs and ranavirus, and test response of Plethodon species to both pathogens in experiments.
Additionally, other as yet identified pathogens might be involved in the population declines. For example, the mysterious 42-bp consensus sequence we generated using Bd- specific primers from nine museum specimens may represent cryptic diversity of Bd in the eastern US, or it may simply be a spurious result from performing PCR on ancient DNA; we are actively investigating this.
Climate change may also be responsible for the observed Plethodon population declines. Recent work  presented evidence collected from these same surveys that populations of several Plethodon species are experiencing reductions in body size, with greater reduction in areas that have experienced warmer and drier conditions. This reduced body size may be related to the reduced abundance and occupancy in Plethodon populations , .
Summary and Conclusion
Our extensive sampling across 6 decades, 767 km, 12 Plethodon taxa and 1400+ individuals was sufficient to have detected Bd if it were present in Appalachian Plethodon salamanders, at least as we currently understand Bd disease dynamics in wild populations (e.g., , ). Therefore, we conclude that it is not a recent introduction of Bd that is responsible for the Appalachian Plethodon salamander declines. We also conclude that it is unlikely Bs or ranavirus given the lack of detection of these pathogens in 2011 field samples. Yet, widespread declines in amphibian populations are occurring across the United States  and globally , . The need to identify the cause and timing of Plethodon salamander declines as well as enigmatic amphibian declines in the US and globally is critical for prioritizing conservation efforts.
Site and species summary of salamanders tested for Bd. Number in parentheses indicate samples tested for both Bs and ranavirus.
We are grateful to R. Highton for his extensive knowledge and detailed collections. We thank A. Wynn, S. Gotte and J. Jacobs (USNM) for permission to swab specimens and for providing detailed data on specimens and collecting localities. We thank P. Langhammer (ASU) and B. Talley (SIU) for contributing Bd positive frog samples, N. McInerney (SCBI-CCEG) for lab assistance, A. Longo (Cornell) for Bd standards, and K. Richards-Hrdlicka (Yale) for assistance with museum Bd lab methods.
Conceived and designed the experiments: CM NMC RCF RWM KRL. Performed the experiments: CM NMC. Analyzed the data: CM KRL. Contributed reagents/materials/analysis tools: RCF RWM KRL. Contributed to the writing of the manuscript: CM NMC RCF RWM KRL. Granted permission to use collections at the National Museum of Natural History for sampling specimens: RWM.
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