9 Jul 2010: Tobler U, Schmidt BR (2010) Correction: Within- and Among-Population Variation in Chytridiomycosis-Induced Mortality in the Toad Alytes obstetricans. PLOS ONE 5(7): 10.1371/annotation/3708df43-0eb2-44bf-8589-a153c199d35d. doi: 10.1371/annotation/3708df43-0eb2-44bf-8589-a153c199d35d View correction
Chytridiomycosis is a fungal disease linked to local and global extinctions of amphibians. Susceptibility to chytridiomycosis varies greatly between amphibian species, but little is known about between- and within-population variability. However, this kind of variability is the basis for the evolution of tolerance and resistance evolution to disease.
In a common garden experiment, we measured mortality after metamorphosis of Alytes obstetricans naturally infected with Batrachochytrium dendrobatidis. Mortality rates differed significantly among populations and ranged from 27 to 90%. Within populations, mortality strongly depended on mass at and time through metamorphosis.
Although we cannot rule out that the differences observed resulted from differences in skin microbiota, different pathogen strains or environmental effects experienced by the host or the pathogen prior to the start of the experiment, we argue that genetic differences between populations are a likely source of at least part of this variation. To our knowledge, this is the first study showing differences in survival between and within populations under constant laboratory conditions. Assuming that some of this intraspecific variation has a genetic basis, this may suggest that there is the potential for the evolution of resistance or tolerance, which might allow population persistence.
Citation: Tobler U, Schmidt BR (2010) Within- and Among-Population Variation in Chytridiomycosis-Induced Mortality in the Toad Alytes obstetricans. PLoS ONE 5(6): e10927. doi:10.1371/journal.pone.0010927
Editor: Carlos A. Navas, University of Sao Paulo, Brazil
Received: March 16, 2010; Accepted: May 8, 2010; Published: June 2, 2010
Copyright: © 2010 Tobler, Schmidt. 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: The study was financed by the following institutions and foundations: the Zoological Institute and the Forschungskredit of the University of Zurich, Vontobel Stiftung, Janggen-Poehn Stiftung, Basler Stiftung fuer biologische Forschung, Stiftung Dr. Joachim De Giacomi, Zoo Zuerich, Gruen Stadt Zuerich, European Union of Aquarium Curators, and Zuercher Tierschutz. 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.
Emerging infectious diseases can represent an important threat to biodiversity and wildlife . Although extinction by disease is a rare event and unlikely in most systems, certain conditions can increase the risk of local or even global extinction by disease: a sympatric host that acts as a reservoir for the pathogen, disease transmission that is frequency-dependent, or disease that drives local populations to such low densities that stochastic factors become important .
Chytridiomycosis, a disease caused by the chytrid fungus Batrachochytrium dendrobatidis (Bd hereafter), is a disease of amphibians that may cause extinctions because it fulfils all three conditions: It infects a variety of hosts with different susceptibilities, some of them acting as reservoirs , transmission is frequency-dependent at low densities , and amphibians often occur in small populations that are prone to stochastic effects . Accordingly, chytridiomycosis has been linked to local and global extinctions of amphibians in Central America, Australia and Europe since its discovery in 1998 .
Susceptibility to Bd and chytridiomycosis varies greatly among amphibian species  and much research has been devoted to the identification of the causes of this variability (e.g. , , ). This line of research helps to identify which species are at risk from Bd . While some species seem to have disappeared completely following Bd invasion , populations of other species have persisted , , , suggesting that there is variation in susceptibility to disease within species. Here we focus on within-species variation in susceptibility to chytridiomycosis because this kind of variability is the raw material for the possible evolution of resistance or tolerance  to Bd, and hence population persistence , , . As no methods are available yet to treat amphibian populations in the field against Bd, susceptible species may persist only where conditions are not favourable for Bd or for disease outbreaks , , or when they can evolve an evolutionary response to the threat imposed by the emergence of chytridiomycosis. The latter may include evolutionary change in defensive skin peptides. Nevertheless, only few studies have addressed within-species variation in susceptibility to this disease and none has looked at the genetic basis of this variation , , .
One of the species that is known to be highly susceptible to chytridiomycosis is the common midwife toad, Alytes obstetricans. The species is widespread across Europe and has suffered substantial declines throughout its range . It was the first species to decline in Europe as a result of mass die-offs after the emergence of Bd . In Spain, mortality almost exclusively affected recently metamorphosed individuals of this species, as the adults are strongly terrestrial and have a low risk of infection. Chytridiomycosis-induced mortality is strongly associated with cold and moist conditions at the time of metamorphosis , . Midwife toads have also suffered strong declines in Switzerland, where more than 50% of the populations went extinct over the last quarter century . Bd is present and widespread in Switzerland (, U. Tobler & B. R. Schmidt, unpublished data).Yet, in the field, no mass mortality has been observed. Only four dead metamorphs were found in the field so far, all of which exhibited high zoospore loads as determined by rt-PCR (B. R. Schmidt & U. Tobler, unpublished data).
The aim of our study was to quantify the impact of Bd and variation thereof on midwife toad populations by measuring post-metamorphic survival of infected individuals in a common garden laboratory experiment. We demonstrate that Bd is linked to mortality under laboratory conditions and that mortality varies greatly among populations. We also identify correlates of mortality among individuals within populations.
Materials and Methods
We collected one-year old tadpoles of Alytes obstetricans shortly after hibernation in 2008 from three sites in Switzerland, two of which were located in canton Baselland and one in canton St. Gallen. Standard hygiene protocols were followed during field work to avoid the spread of Bd and other pathogens . The sites were chosen because 1) we knew they sustained large tadpole numbers and 2) they were positive for Bd . The first site in Baselland (7.783306°E, 47.459667°N, 410 masl, hereafter referred to as BLI) is located in a former quarry and consists of three main water bodies, in only two of which tadpoles were caught. The larger pond is about 16 m2 in size, 0.8 m deep and is densely vegetated; the smaller pond is 8 m2 in size, 0.5 m in depth, and has very little vegetation but has reed along the edges. The second site in Baselland (7.801185°E, 47.436677°N, 480 masl, hereafter referred to as BLZ) is a forest pond approximately 300 m2 in size and 2.5 m in depth. The site in St. Gallen (9.533416°E, 47.381742°N, 540 masl, hereafter referred to as SGA) is a garden at the south-eastern distribution border of the species. The population is larger than 20 calling males, and three small garden ponds (2–5 m2 in size, 0.2–0.5 m in depth) serve as breeding sites.
Laboratory experiment: treatments
Bd only infects keratinised skin of amphibians  and infection in tadpoles is restricted to the mouthparts, which does not cause disease. However, during metamorphosis, the skin becomes keratinised, and the pathogen can then spread over the whole body and cause hyperkeratosis and osmotic imbalance, leading to death , . Recently metamorphosed individuals are most susceptible to disease, supposedly due to a downregulation of immune defences during metamorphosis . Thus, we measured differences in post-metamorphosis survival of Bd-positive and -negative Alytes tadpoles from the three populations. Because all tadpoles were tested for Bd infection with rt-PCR  and confirmed positive initially, we assigned them to three different treatments in order to obtain one Bd-negative control: 1) The “Itraconazole treatment” group served as a Bd-free control. Individuals were treated with Itraconazole (1 mg/L; Sporanox, Janssen-Cilag) for 5 minutes per day over the course of seven days to clear the infection. We followed the protocol developed by Garner et al.  which had been successfully used for the treatment of Alytes muletensis tadpoles against Bd; unlike Garner et al. , we observed no depigmentation. The tadpoles were returned to the same container after treatment, which had been rinsed with boiling water during the Itraconazole bath. 2) Because the tadpoles were exposed to low water levels and frequent capture during the Itraconazole treatment, we designed the “infected handled treatment” as a control for stress during handling. The tadpoles were treated in exactly the same way as the Itraconazole treatment, but instead of an Itraconazole solution, tap water was used. 3) The “infected unhandled” group was not handled apart from the regular water change and feeding and was left infected throughout the experiment.
To test for differences in survival among populations, we assigned equal numbers of tadpoles from the three populations to the three treatments. We balanced body mass among treatments within populations.
Laboratory experiment: procedures
We caught 143 tadpoles (50 from BLI, 43 from BLZ and 50 from SGA) in April 2008 and brought them to the laboratory, where they were placed in individual one-litre plastic containers filled with tap water and a single dried beech tree (Fagus sp.) leaf. The laboratory was equipped with full spectrum sunlight lamps, and we used a daylength of 16 hours and kept the room at 19–21°C. Throughout the course of the experiment, we changed the water in the containers twice a week and added food containing Spirulina algae (Tetra Pleco Wafer, Tetra Germany, Spectrum Brands Inc.) ad libitum three times a week. In the week following capture, the tadpoles were weighed to the nearest 0.01 g (Scaletec Instruments, Heiligenstadt, Germany), measured from the snout to the beginning of the tail muscle to the nearest 0.1 mm, and swabbed over the mouth parts with a sterile cotton swab (Copan Italia S.p.A., Brescia, Italy). Further swabs were taken when metamorphosis was finished (Gosner stage 46, ) and (3) upon death or 30 days after stage 42. Size measurements were repeated three times during the experiment: (1) when the larvae entered metamorphosis (Gosner stage 42), (2) when metamorphosis was finished (Gosner stage 46) and (3) upon death or 30 days after stage 42. We used separate pairs of gloves for handling and separate plastic beakers for weighing each tadpole. When the tadpoles entered metamorphosis (Gosner stage 42), the containers were drained of most of the water and tilted, so that both land and water were available to the toadlets. We put a moist paper towel at the bottom of each container. When the metamorphosis was complete (Gosner stage 46), we fed the toadlets crickets of adequate size ad libitum three times a week. For each individual, the experiment was ended 30 days after stage 42 or upon death.
We analysed the swabs for the presence of Bd with Bd-specific primers in rt-PCR following the protocol by Boyle et al.  with slight modifications: samples were run in duplicates and when the two PCR-wells retuned inconsistent results, the analysis was repeated. Because the extraction reagent is inhibitory to the PCR reaction, samples were diluted 1∶10 prior to rt-PCR analysis. As in Boyle et al. , we report untransformed zoospore equivalents. Reactions yielding 0.1 genomic equivalents (GE; untransformed value) or above were considered Bd-positive. This threshold was used to classify individuals as either “infected” or “not infected”. For the statistical analyses, however, we used zoospore loads rather than the categories “infected” or “not infected”.
We tested for differences in body length among the different populations at three stages during development: at the beginning of the experiment, at stage 42 (beginning of metamorphosis) and at stage 46 (end of metamorphosis) using separate ANOVA, and we tested for correlations between body mass and length at stage 42, 46 and the end of the experiment. Because mass and length were strongly correlated, we only used body mass for subsequent analyses.
To analyse survival data we used the Cox proportional hazard model. This model assumes an underlying hazard function describing how hazard changes over time, and fits effect parameters using Cox's likelihood. Individual survival times are censored, which means that individuals may die after the end of the study period. We tested for overall differences in mortality between treatments and populations using daily counts on the number of survivors until 30 days after beginning of metamorphosis (Gosner stage 42). To test for the effects of individual condition and environmental effects on hazard risk, we did a Cox proportional hazard model with the two infected treatments only. The variables on individual condition included were body mass at the beginning of the experiment, at stage 42, 46 and at the end or death, and time through metamorphosis; the variables for environmental effects were zoospore loads at the beginning, at stage 46, at the end and time to metamorphosis. We also included interactions between zoospore loads and population.
Because individuals that survived until the end of the experiment had more time to gain mass, we tested the correlation between body mass and time since metamorphosis with a Pearson correlation test. All tests were performed in R, version 2.8.1 .
Populations differed significantly in body mass at the beginning the experiment (ANOVA for mass at beginning of the experiment and at stage 42: both p<0.001) but not at metamorphosis (ANOVA at stage 46: p = 0.144; Figure 1). Body length and mass were strongly correlated at all stages (Pearson correlation for beginning, stage 42, stage 46 and end of experiment; rbeginning = 0.83, rstage_42 = 0.76, rstage_46 = 0.30, rend = 0.90; all p<0.001).
Boxplots showing body mass of the different populations at the beginning of the experiment, at the start of metamorphosis (Gosner stage 42) and at the end of metamorphosis (Gosner stage 46). The black line represents the median, the box represents the interquartile range containing 50% of the values, and whiskers mark the 1.5 fold interquartile range. Outliers are marked with circles. Grey boxes = survivors, white boxes = non-survivors.
All 143 overwintered tadpoles were infected with Bd at the time of capture. When they completed metamorphosis (Gosner stage 46), all Itraconazole-treated tadpoles were Bd-negative while all infected unhandled or infected handled tadpoles were still infected. Eight tadpoles died during the course of the experiment before undergoing metamorphosis: Two tadpoles from BLI died before treatment assignment within a week after capture, and another tadpole from BLI died in the unhandled group. Two tadpoles from BLZ died in the Itraconazole group, and from SGA one tadpole died in the Itraconazole treatment and two from the infected handled treatment, the last five all within 1.5 weeks after treatment. Because chytridiomycosis usually does not cause mortality during the larval stage and most deaths were probably caused by transportation or handling stress, these 8 tadpoles were excluded from the analyses. The remaining 135 tadpoles reached Gosner stage 42 (beginning of metamorphosis) 25 to 129 days after 25 April, when the first swab was collected (and 32–136 days after capture). From stage 42 on, it took them seven to 18 days (mean±SD: 12±2) to fully resorb the tail.
All Itraconazole-treated toadlets survived until the end of the experiment; mortality only occurred in infected toadlets. Across all populations, only 34.1% (31 out of 90) of infected (handled and unhandled) metamorphs survived until 30 days after stage 42; those that died survived on average for 8.6±6.5 days post-metamorphosis only.
Infected animals that died showed disease symptoms typical of chytridiomycosis shortly before death . Diseased individuals stopped feeding approximately one day prior to death but did not show any other symptoms until less than a day before they died. Only within a few hours to death they would become lethargic and loose their righting reflex, at the same time they started to shed skin heavily when touched. Although we did not investigate dead individuals histologically to confirm that chytridiomycosis was the cause of death, disease symptoms and severity of infection as quantified by rt-PCR shortly before or after death, respectively, suggest that chytridiomycosis was the cause of death.
The Cox proportional hazard test revealed a significant effect of treatment (p<0.001) and population (p<0.001) on survival (Figure 2). Survival differed between infected and uninfected individuals, but not between the infected unhandled and the infected handled group (unhandled: 33.5±29.1%, handled: 32.6±43.9%). Population BLI differed from the two other populations in survival among infected individuals (i.e. confidence intervals did not overlap; BLI: 75±2.0% (SE), BLZ: 14.6±1.9%, SGA: 9.6±0.7%), but there was no difference in survival between SGA and BLZ. Because the handled and unhandled group did not differ in survival, they were pooled for subsequent analyses.
Cox regression on survival depending on treatment and population. The blue line represents the Itraconazole treatment for all populations. Yellow = infected handled, red = infected unhandled. Continuous line = population BLI, dashed line = population BLZ, dotted line = population SGA.
In the infected treatment groups, heavier individuals survived better (Cox proportional hazard test, Figure 3, Table 1); body mass at the end of the experiment strongly correlated with life span since stage 46 (Pearson correlation, p<0.001). Survivors completed metamorphosis slightly slower than individuals that died later on (survivors: 12.9±2.8 (SD) days, non-survivors: 12.3±2.6 days, Table 1). Although infection load at any stage did not affect individual hazard risk (Cox proportional hazard test, Table 1), non-survivors had on average higher zoospore loads (9701 GE±21726.2) than survivors (28.2 GE±113.2; Figure 4) at death or at the end of the experiment, respectively. There was an interaction between zoospore load and population (Table 1, Figure 4). Three individuals out of 31 survivors had cleared infection below the detection threshold.
Boxplots showing body mass of infected individuals at the beginning of metamorphosis (Gosner stage 42), at the end of metamorphosis (Gosner stage 46) and at the end of the experiment or death. Grey boxes = survivors, white boxes = non-survivors. The black line represents the median, the box represents the interquartile range containing 50% of the values, and whiskers mark the 1.5 fold interquartile range. Outliers are marked with circles. Grey boxes = survivors, white boxes = non-survivors.
Infection load, measured in genomic equivalents from rt-PCR reactions and logarithmically transformed, in individuals from the infected treatments at the end of experiment. The black line represents the median, the box represents the interquartile range containing 50% of the values, and whiskers mark the 1.5 fold interquartile range. Outliers are marked with circles. Grey boxes = survivors, white boxes = non-survivors.
Here we show that under laboratory conditions, mortality in Bd-infected metamorphs was population-specific and varied from 27% to 90%. Our experiment thus confirms that Bd infection was linked to substantial mortality in Alytes toadlets from populations where no mass mortality events caused by chytridiomycosis have been reported even though Bd is widespread (, U. Tobler and B. R. Schmidt, unpublished data). If the observed mortality is representative of Bd-induced mortality in the field, such high levels of mortality may lead to population declines , .
How could such populations persist? Sensitivity analyses of amphibian life histories suggest that post-metamorphic juvenile survival appears to determine the fate of the populations. High levels of mortality may lead to population declines , . In contrast, Briggs et al.  modelled the effects of Bd on population dynamics and predicted population persistence if some infected individuals survive. Because no data on population trends are available for the populations that we studied, we cannot tell whether they currently undergo declines. To predict the fate of our study populations, more data would be necessary. For example, it is unknown (1) for how long Bd has been present in these populations, (2) how long after the onset of chytridiomycosis the adult populations are expected to decline, (3) whether and how strongly mortality rates differ between years and (4) whether density dependence in the adult stage could dampen the effects of Bd-associated mortality immediately after metamorphosis.
To our knowledge, this is the first study to show differences in the survival of Bd-infected individuals both within and between populations in the laboratory. We do not know why individuals and populations differed in susceptibility. Some variation may be attributable to variation among individuals in growth (i.e., mass at metamorphosis) and development (i.e., duration of metamorphosis; , Table 1 and Figure 3), although the large difference in body mass at the end of the experiment mostly resulted from the longer lifespan of survivors (Figure 4). Survivors and non-survivors differed in the duration of metamorphosis (Table 1). Duration of metamorphosis may be an important determinant of how quickly the immune system recovers after metamorphosis . A better understanding of how duration of metamorphosis affects Bd-associated mortality would be a worthwhile topic for further study. Variation in mass and survival may have been caused by differential environmental conditions early in the larval stage, by variation in the tadpole immune system (i.e. genetic variation at disease resistance or tolerance loci, antimicrobial peptides and symbiotic bacteria), because of differences between Bd strains from the tadpoles' sites of origin or because of infection of single vs. multiple Bd strains.
We do not expect that environmental conditions experienced early in life affected the outcome of the experiment. The tadpoles were captured after hibernation. We kept them in the laboratory under common garden conditions for 4 to 18 weeks before they started metamorphosis. Because effects of previously experienced environmental conditions often fade out quickly  and because the common conditions in the laboratory experiment would minimise environmental variation, the effects of previously experienced environmental conditions in the ponds of origin should be minimal.
The immunocompetence is likely to have varied among individuals and populations. While we know little about the genetic basis of the immune system in amphibians , we know that antimicrobial peptides and symbiotic bacteria that are active against Bd may vary both among individuals and populations , . Strains of Bd are known to differ in how much mortality they inflict on amphibians  and multiple strains of Bd may occur within the same locality , . Infection with multiple strains might affect virulence , . We did not test whether tadpoles in our experiment had the same Bd strain(s), antimicrobial peptides, or bacteria. We know, however, that the bacterial communities differ between the populations BLI and BLZ (L. Davis, personal communication).Whether and how the bacterial communities found at each site differ in their Bd-inhibitory effects is the subject of current research (L. Davis, personal communication). For logistic reasons during experimental work, the same equipment was used for water changes for all populations within one treatment, and thus bacterial communities and pathogen strains may have been homogenised. Nevertheless, skin microbiota may account for some of the variation in survival that we observed . We suggest that some of the variation in mortality among populations that we observed in the common garden experiment is due to genetic differences among populations. This is the usual interpretation of among-population variation in common garden experiments. Two lines of evidence support this suggestion. First, we know that the host populations are genetically differentiated (pairwise FST based on 12 microsatellites ≥0.19, U. Tobler & B. R. Schmidt, unpublished data). Second, individual differences in growth (mass at metamorphosis) did affect survival; among-population variation in life history traits can have a genetic basis . Considering this, genetic differences among populations may at least partially explain the observed differences in mortality, as it is often the case in host-parasite associations , .
A number of experimental studies reported that many Bd-infected amphibians can survive or even clear infection (see electronic appendix to reference ). For example, Fisher et al.  reported that host survival varied in a dose-dependent manner among Bd strains. In most cases, a substantial proportion of hosts survived (as in our experiment; Figure 1). Nevertheless, Bd imposes strong selection on amphibian hosts. If variation in susceptibility to Bd has a genetic basis, we would expect to see genetic changes in the host population and ultimately the evolution of resistance or tolerance to Bd , , . Such pathogen-mediated selection is known to occur in amphibians: Tennessen and Blouin  and Teacher et al.  showed that there is natural selection on the genetic diversity of antimicrobial peptides and MHC alleles, respectively. One interpretation of among-population variation in Bd-associated mortality reported in Figure 1 is that the populations we studied may already differ in their degree of tolerance or resistance to Bd.
While strategies to manage Bd in the wild are still being developed , , we suggest that enhancing an evolutionary response of amphibians to Bd, may be a worthwhile conservation strategy to mitigate the effects of the disease . The model by Briggs et al.  suggests that amphibian populations can persist or even recover if some individuals loose the infection. Such a “waiting for resistance or tolerance to evolve” strategy may be risky, however, as some hosts may fail to evolve adaptations to novel pathogens . First, rapid disease emergence may cause amphibian populations to go extinct in many places before resistance or tolerance allowing for population persistence can evolve , , . Second, Bd is likely to evolve counteradaptations to host resistance . Yet, if Bd and amphibian hosts would enter a coevolutionary process, then extinction–as commonly observed in areas where Bd emerged–may become a less likely outcome.
In summary, our experiment demonstrates that within a species, mortality can greatly differ both at the population and individual level, and that these different mortalities are not necessarily due to climatic variation at the time of metamorphosis because in this case they were observed under stable laboratory conditions. The results also show that Bd-associated mortality can be substantial in an area where Bd is widespread (, , U. Tobler and B. R. Schmidt, unpublished data) but where no mass mortalities or Bd-associated population declines have been reported . Nevertheless, the high mortality rates we observed are likely to affect populations and suggest that Bd may be a cryptic driver of amphibian population dynamics. The mechanisms how amphibian populations can cope with additional mortality due to chytridiomycosis are unknown. We argue that in many situations, global or local extinction will only occur if aided by other threats such as habitat degradation, demographic stochasticity or unusual weather conditions. We suggest that conservation measures should prioritise populations that have high resistance or tolerance against chytridiomycosis to prevent the loss of these populations by other threats. In the long term it is desirable to determine what factors are involved in population level disease resistance or tolerance in order to allow the transfer of resistance mechanisms, such as resistant genotypes or symbiotic skin microbiota, into non-resistant populations. This may enable the management of amphibian populations, or their habitat, to increase survival rates and thus allow long-term population survival in the presence of novel disease threats.
We are grateful to Simone Baumgartner and Jos Kielgast for support during practical experimental work and to Doug Woodhams and Leyla Davis for insights into and discussions on frog skin microbiota. We thank Ditte Christiansen, Corina Geiger, Trent Garner and Christoph Vorburger for helpful comments on the manuscript.
Conceived and designed the experiments: UT BRS. Performed the experiments: UT. Analyzed the data: UT BRS. Wrote the paper: UT BRS.
- 1. Daszak P, Cunningham AA, Hyatt AD (2000) Wildlife ecology-Emerging infectious diseases of wildlife-Threats to biodiversity and human health. Science 287: 443–449.
- 2. de Castro F, Bolker B (2005) Mechanisms of disease-induced extinction. Ecol Lett 8: 117–126.
- 3. Fisher MC, Garner TWJ, Walker SF (2009) Global emergence of Batrachochytrium dendrobatidis and amphibian chytridiomycosis in space, time, and host. Annu Rev Microbiol 63: 291–310.
- 4. Rachowicz LJ, Briggs CJ (2007) Quantifying the disease transmission function: effects of density on Batrachochytrium dendrobatidis transmission in the mountain yellow-legged frog Rana muscosa. J Anim Ecol 76: 711–721.
- 5. Green DM (2003) The ecology of extinction: population fluctuation and decline in amphibians. Biol Conserv 111: 331–343.
- 6. Skerratt LF, Berger L, Speare R, Cashins S, McDonald KR, et al. (2007) Spread of chytridiomycosis has caused the rapid global decline and extinction of frogs. EcoHealth 4: 125–134.
- 7. Kilpatrick AM, Briggs CJ, Daszak P (2010) The ecology and impact of chytridiomycosis: an emerging disease of amphibians. Trends Ecol Evol 25: 109–118.
- 8. Woodhams DC, Rollins-Smith LA, Carey C, Reinert L, Tyler MJ, et al. (2006) Population trends associated with skin peptide defenses against chytridiomycosis in Australian frogs. Oecologia 146: 531–540.
- 9. Brucker RM, Harris RN, Schwantes CR, Gallaher TN, Flaherty DC, et al. (2008) Amphibian chemical defense: antifungal metabolites of the microsymbiont Janthinobacterium lividum on the salamander Plethodon cinereus. J Chem Ecol 34: 1422–1429.
- 10. Rowley JJL, Alford RA (2007) Behaviour of Australian rainforest stream frogs may affect the transmission of chytridiomycosis. Dis Aquat Org 77: 1–9.
- 11. Bielby J, Cooper N, Cunningham AA, Garner TWJ, Purvis A (2008) Predicting susceptibility to future declines in the world's frogs. Conserv Lett 1: 82–90.
- 12. Lips KR, Brem F, Brenes R, Reeve JD, Alford RA, et al. (2006) Emerging infectious disease and the loss of biodiversity in a Neotropical amphibian community. Proc Natl Acad Sci U S A 103: 3165–3170.
- 13. Briggs CJ, Vredenburg VT, Knapp RA, Rachowicz LJ (2005) Investigating the population-level effects of chytridiomycosis: An emerging infectious disease of amphibians. Ecology 86: 3149–3159.
- 14. Retallick RWR, McCallum H, Speare R (2004) Endemic infection of the amphibian chytrid fungus in a frog community post-decline. PLoS Biol 2: 1965–1971.
- 15. Murray KA, Skerratt LF, Speare R, McCallum H (2009) Impact and dynamics of disease in species threatened by the amphibian chytrid fungus, Batrachochytrium dendrobatidis. Conserv Biol 23: 1242–1252.
- 16. Roy BA, Kirchner JW (2000) Evolutionary dynamics of pathogen resistance and tolerance. Evolution 54: 51–63.
- 17. Miller MP, Vincent ER (2008) Rapid natural selection for resistance to an introduced parasite of rainbow trout. Evol Appl 1: 336–341.
- 18. Bell G, Collins S (2008) Adaptation, extinction and global change. Evol Appl 1: 3–16.
- 19. Spielman D, Brook BW, Briscoe DA, Frankham R (2004) Does inbreeding and loss of genetic diversity decrease disease resistance? Conserv Genet 5: 439–448.
- 20. Bosch J, Carrascal LM, Duran L, Walker S, Fisher MC (2007) Climate change and outbreaks of amphibian chytridiomycosis in a montane area of Central Spain; is there a link? Proc R Soc Biol Sci Ser B 274: 253–260.
- 21. Walker SF, Bosch J, Gomez V, Garner TWJ, Cunningham AA, et al. (2010) Factors driving pathogenicity vs. prevalence of amphibian panzootic chytridiomycosis in Iberia. Ecol Lett 13: 372–382.
- 22. Lam BA, Walke JB, Vredenburg VT, Harris RN (2010) Proportion of individuals with anti-Batrachochytrium dendrobatidis skin bacteria is associated with population persistence in the frog Rana muscosa. Biol Conserv 143: 529–531.
- 23. Tennessen JA, Woodhams DC, Chaurand P, Reinert LK, Billheimer D, et al. (2009) Variations in the expressed antimicrobial peptide repertoire of northern leopard frog (Rana pipiens) populations suggest intraspecies differences in resistance to pathogens. Developmental and Comparative Immunology 33: 1247–1257.
- 24. Bosch J, Beebee T, Schmidt BR, Tejedo M, Martinez-Solano I, et al. (2008) Alytes obstetricans. IUCN 2009 IUCN Red LIst of Threatened Species Version 20092: downloaded on 19 January 2010.
- 25. Bosch J, Martinez-Solano I, Garcia-Paris M (2001) Evidence of a chytrid fungus infection involved in the decline of the common midwife toad (Alytes obstetricans) in protected areas of central Spain. Biol Conserv 97: 331–337.
- 26. Schmidt BR, Zumbach S (2005) Rote Liste der gefährdeten Amphibien der Schweiz. Bundesamt für Umwelt, Land und Landschaft and Koordinationsstelle Amphibien- und Reptilienschutz in der Schweiz, Bern.
- 27. Garner TWJ, Walker S, Bosch J, Hyatt AD, Cunningham AA, et al. (2005) Chytrid fungus in Europe. Emerg Infect Dis 11: 1639–1641.
- 28. Schmidt BR, Furrer S, Kwet A, Lötters S, Rödder D, et al. (2009) Desinfektion als Massnahme gegen die Verbreitung der Chytridiomykose bei Amphibien. In: Hachtel M, Schlüpmann M, Thiesmeier B, Weddling K, editors. Methoden der Feldherpetologie. pp. 229–241. Bielefeld.
- 29. Longcore JE, Pessier AP, Nichols DK (1999) Batrachochytrium dendrobatidis gen. et sp. nov., a chytrid pathogenic to amphibians. Mycologia 91: 219–227.
- 30. Berger L, Speare R, Daszak P, Green DE, Cunningham AA, et al. (1998) Chytridiomycosis causes amphibian mortality associated with population declines in the rain forests of Australia and Central America. Proc Natl Acad Sci U S A 95: 9031–9036.
- 31. Voyles J, Young S, Berger L, Campbell C, Voyles WF, et al. (2009) Pathogenesis of chytridiomycosis, a cause of catastrophic amphibian declines. Science 326: 582–585.
- 32. Rollins-Smith LA (1998) Metamorphosis and the amphibian immune system. Immunol Rev 166: 221–230.
- 33. Boyle DG, Boyle DB, Olsen V, Morgan JAT, Hyatt AD (2004) Rapid quantitative detection of chytridiomycosis (Batrachochytrium dendrobatidis) in amphibian samples using real-time Taqman PCR assay. Dis Aquat Org 60: 141–148.
- 34. Garner TWJ, Garcia G, Carroll B, Fisher MC (2009) Using itraconazole to clear Batrachochytrium dendrobatidis infection, and subsequent depigmentation of Alytes muletensis tadpoles. Dis Aquat Org 83: 257–260.
- 35. Gosner KL (1960) A simplified table for staging anuran embryos and larvae with notes on identification. Herpetol J 16: 183–190.
- 36. R Development Core Team (2008) R: A language and environment for statistical computing. R Foundation for Statistical Computing, Vienna, Austria. ISBN 3-900051-07-0, URL http://www.R-project.org.
- 37. NSW National Parks and Wildlife Service (2001) Hygiene protocol for the control of disease in frogs. Information Circular Number 6. NSW NPWS, Hurstville NSW.
- 38. Lampo M, De Leo GA (1998) The invasion ecology of the toad Bufo marinus: from South America to Australia. Ecol Appl 8: 388–396.
- 39. Hels T, Nachman G (2002) Simulating viability of a spadefoot toad Pelobates fuscus metapopulation in a landscape fragmented by a road. Ecography 25: 730–744.
- 40. Garner TWJ, Walker S, Bosch J, Leech S, Rowcliffe JM, et al. (2009) Life history tradeoffs influence mortality associated with the amphibian pathogen Batrachochytrium dendrobatidis. Oikos 118: 783–791.
- 41. Van Buskirk J (2002) Phenotypic lability and the evolution of predator-induced plasticity in tadpoles. Evolution 56: 361–370.
- 42. Richmond JQ, Savage AE, Zamudio KR, Rosenblum EB (2009) Toward immunogenetic studies of amphibian chytridiomycosis: linking innate and acquired immunity. Bioscience 59: 311–320.
- 43. Harris RN, Brucker RM, Walke JB, Becker MH, Schwantes CR, et al. (2009) Skin microbes on frogs prevent morbidity and mortality caused by a lethal skin fungus. Isme J 3: 818–824.
- 44. Tennessen JA, Blouin MS (2008) Balancing selection at a frog antimicrobial peptide locus: fluctuating immune effector alleles? Mol Biol Evol 25: 2669–2680.
- 45. Fisher MC, Bosch J, Yin Z, Stead DA, Walker J, et al. (2009) Proteomic and phenotypic profiling of the amphibian pathogen Batrachochytrium dendrobatidis shows that genotype is linked to virulence. Mol Ecol 18: 415–429.
- 46. Goka K, Yokoyama J, Une Y, Kuroki T, Suzuki K, et al. (2009) Amphibian chytridiomycosis in Japan: distribution, haplotypes and possible route of entry into Japan. Mol Ecol 18: 4757–4774.
- 47. Alizon S (2008) Decreased overall virulence in coinfected hosts leads to the persistence of virulent parasites. Am Nat 172: E67–E79.
- 48. Ebert D, Zschokke-Rohringer CD, Carius HJ (2000) Dose effects and density-dependent regulation of two microparasites of Daphnia magna. Oecologia 122: 200–209.
- 49. Laugen AT, Kruuk LEB, Laurila A, Räsänen K, Stone J, et al. (2005) Quantitative genetics of larval life-history traits in Rana temporaria in different environmental conditions. Genet Res 86: 161–170.
- 50. Ebert D, Zschokke-Rohringer CD, Carius HJ (1998) Within- and between-population variation for resistance of Daphnia magna to the bacterial endoparasite Pasteuria ramosa. Proc R Soc Biol Sci Ser B 265: 2127–2134.
- 51. Cory JS, Myers JH (2009) Within and between population variation in disease resistance in cyclic populations of western tent caterpillars: a test of the disease defence hypothesis. J Anim Ecol 78: 646–655.
- 52. Haag CR, Ebert D (2004) Parasite-mediated selection in experimental metapopulations of Daphnia magna. Proc R Soc Biol Sci Ser B 271: 2149–2155.
- 53. Zbinden M, Haag CR, Ebert D (2008) Experimental evolution of field populations of Daphnia magna in response to parasite treatment. J Evol Biol 21: 1068–1078.
- 54. Teacher AGF, Garner TWJ, Nichols RA (2009) Evidence for directional selection at a novel Major Histocompatibility Class I marker in wild Common frogs (Rana temporaria) exposed to a viral pathogen (Ranavirus). PLoS One 4: 1–6.
- 55. Kilpatrick AM (2006) Facilitating the evolution of resistance to avian malaria in Hawaiian birds. Biol Conserv 128: 475–485.
- 56. Gomulkiewicz R, Houle D (2009) Demographic and genetic constraints on evolution. Am Nat 174: E218–E229.
- 57. Orr AH, Unckless RL (2008) Population extinction and the genetics of adaptation. Am Nat 172: 160–169.