The Coeur d’Alene salamander (Plethodon idahoensis) is a species of special concern throughout its global range, which includes southeastern BC (COSEWIC, Nov 2007), Idaho, and Montana, due to disjunct populations and sensitivity to human disturbance. Within the Interior Cedar-Hemlock forest on Mount Revelstoke, BC, Coeur d’Alene salamanders occur at their highest abundance between 600 m and 800 m. Beyond the Mount Revelstoke National Park boundaries, the low-order stream habitat of this species is subject to disturbance from forestry, mining, road building, road maintenance, and watercourse diversions such as run-of-the-river hydro projects. We conducted nocturnal salamander surveys and assessed habitat characteristics on 12 Sites (750 m² – 1000 m² stream transects) along three streams from June through September 2006. Coeur d’Alene salamanders were detected from 600 m - 1000 m on seven of the 12 study sites. Relative abundance of Coeur d’Alene salamanders ranged from 0.005 ± 0.001 per m² to 0.025 ± 0.005 per m² on six sites below 950 m. Coeur d’Alene salamanders occurred at an average of 0.001 ± 0.001 per m² at 972 m, the only site above 950 m where we detected salamanders. Our capture-mark-recapture efforts of three surveys per month in June and August yielded a very low recapture rate (3.95 %). Coeur d’Alene salamanders are challenging to enumerate due to their vertical distribution within the soil and underlying geological material. Neonate, juvenile, and adult Coeur d’Alene salamanders were observed from June to September and the highest proportion of neonates occurred in June, soon after the salamanders emerged from winter hibernation. Results of a logistic regression analysis of 1-m² plots reflected the importance of fine scale habitat characteristics (quadrat gradient, boulder, cobble, moss, grass, and shrub) in addition to site-level habitat features (water volume and elevation) that in combination describe the association of Coeur d’Alene salamanders with cool and moist conditions. Coeur d’Alene salamanders appear to select streambed habitat during warm, dry periods, which may be a behavioural response to minimize dehydration during periods of activity at the surface of the forest floor.

Hardwood bottomland ecosystems provide critical habitat for various wildlife among numerous ecosystem services. Since the 1800s, these forested wetlands have been logged and drained for agriculture. The federal government passed a series of legislative acts that protected wetlands and provided monetary support for restoration. The Wetlands Reserve Program (WRP) was established in 1990 with the goal of restoring ecological function in wetlands. Although several studies have measured plant and wildlife responses to WRP restorations, no standard protocol has been developed to monitor the state of ecological restoration at sites. Index of biotic integrity (IBI) models are commonly used to evaluate ecological function by assigning scores derived from biological characteristics measured at disturbed sites and comparing them with reference sites. Therefore, the objectives of my study were to: (1) characterize vegetation, amphibian and bird communities among 17 WRP restoration and 4 reference bottomland sites, and (2) develop IBI models for these communities to use in monitoring ecological restoration. My study was conducted across 10 counties in western Tennessee from March – August 2008, and communities were measured using standard sampling techniques. I detected 15 amphibian and 95 bird species at bottomland WRP sites, which ranged 2 – 21 years old. Anurans were common among sites, but salamanders were only detected at reference sites containing mature forests. The bird community changed predictably in response to succession, with grassland birds dominating young restoration sites and scrub-shrub and forest birds dominating older restoration and reference sites. Vegetation structure was related to site age, and a good predictor of bird community composition. Variables retained in the vegetation IBI model included density of snags, logs and overstory trees, basal area, and percent vertical cover measured using a profile board. The bird IBI model contained relative abundance of bark feeding, branch nesting, and twig nesting guilds. Presence of salamanders was the only variable in the amphibian IBI model. My results indicate that the WRP is contributing to the regional biodiversity of western Tennessee. The IBI models that I developed can be used for monitoring ecological restoration in Tennessee hardwood bottomlands; however, their applicability outside this region should be validated.

Thesis (M.S.)--North Carolina State University, 2003. / Title from PDF title page (viewed on Jan. 13, 2005). Includes vita. Includes bibliographical references (p. 76-86).

Amphibians are declining at alarming rates globally. Multiple factors contribute to these declines, including chemical contaminants and emergent diseases. In recent years, agrochemical use, especially fungicide applications, has increased considerably. Previous studies have demonstrated that these agrochemicals leave application sites and enter wetlands via runoff and have detrimental effects on non-target organisms. For example, exposure to contaminants can have multifarious effects on amphibians, such as reducing their ability to deal with a secondary stressor, such as disease. A pathogen that is found concomitant with chemical contaminants in aquatic systems is Batrachochytrium dendrobatidis (Bd). Bd has decimated amphibian populations worldwide. Susceptibility to this pathogen varies across amphibian life stages, and is greater in adults than larvae. Consequently, it is important to examine the effects of simultaneous and serial Bd and agrochemical exposure throughout amphibian development. I assessed the combined effects of 3 different fungicides and Bd on two amphibian species: Cuban tree frogs (Osteopilus septentrionalis) and grey tree frogs (Hyla versicolor), both simultaneously and across life stages. To elucidate the complexities of these interactions, I conducted two experiments, one in the laboratory and another in outdoor mesocosms. Frogs were exposed to most of the possible combinations of fungicides and Bd as tadpoles and metamorphs. The presence of fungicides during the tadpole stage caused no difference in timing to metamorphosis and therefore no extension of time animals were exposed to the pathogen. Fungicides did not reduce fungal growth; in fact, tadpoles exposed simultaneously to a fungicide and Bd, regardless of the specific fungicide, had increased fungal loads compared to acetone controls. Additionally, animals exposed to both stressors simultaneously had higher mortality compared to controls or any of the stressors singly. Lastly, the fungicide had persistent effects on amphibian health by affecting susceptibility to Bd later in ontogeny. Frogs exposed to any of the three fungicides as a tadpole had higher Bd prevalence, Bd abundance, and Bd-induced mortality when challenged with Bd after metamorphosis, an average of 71 days after their last fungicide exposure. In conclusion, I found no benefits of fungicides for amphibians. In fact, results indicate both immediate and delayed negative effects of exposure to fungicides and Bd. These findings highlight the importance of studying multiple potential contributors to amphibian declines, simultaneously and sequentially, to understand net effects of stressors on amphibian performance.

Amphibians are the most threatened taxon on the planet. Declines have been associated with over-exploitation, habitat loss, pollution, and pathogenic diseases, but of these factors, pollution and disease have been relatively under-studied. Here, I investigated: 1) the impacts of commonly used pesticides on aquatic communities, 2) the effect of these pesticides on amphibian susceptibility to the pathogenic chytrid fungus, Batrachochytrium dendrobatidis (Bd), and 3) whether there are non-amphibian hosts of Bd and 4) how to best quantify the survival of Bd through ontogeny of the host. In my first research chapter, I quantified the effects of environmentally relevant concentrations of the mot commonly used synthetic fungicide in the US, chlorothalonil, on 34 species-, 2 community- and 11 ecosystem-level responses in a multitrophic-level system. Chlorothalonil increased mortality of amphibians, gastropods, zooplankton, algae, and a macrophyte (reducing taxonomic richness), reduced decomposition and water clarity, and elevated dissolved oxygen and net primary productivity. These ecosystem effects were indirect but were predictable based on changes in taxonomic richness. A path analysis suggests that chlorothalonil-induced reductions in biodiversity and top-down and bottom-up effects facilitated algal blooms that shifted ecosystem functions. In my second chapter, I investigated how a wide range of ecologically relevant concentrations of chlorothalonil affected four species of amphibians (Osteopilus septentrionalis, Rana sphenocephala, Hyla squirella and H. cinerea). I also evaluated the effects of chlorothalonil on liver tissue, immune cell density, and the stress hormone, corticosterone. Chlorothalonil killed nearly every amphibian at the expected environmental concentration (EEC) and, at concentrations to which humans are commonly exposed (up to the EEC), it was associated with elevated corticosterone levels and changes in immune cells. Three species (O. septentrionalis, R. sphenocephala, and H. cinerea) showed a non-monotonic dose-response, with low and high concentrations causing significantly greater mortality than intermediate concentrations and controls. Corticosterone exhibited a similar non-monotonic dose response and chlorothalonil concentration was inversely associated with liver tissue and immune cell densities. These studies on chlorothalonil emphasize the need to re-evaluate its safety and to further link anthropogenic-induced changes in biodiversity to altered ecosystem functions. In my third research chapter, I investigated the effects of chlorothalonil and atrazine, one of the most commonly used herbicides in the US, on amphibian susceptibility to Bd, a leading cause of amphibian extinctions. Relative to controls, atrazine monotonically reduced Bd growth in culture and on tadpoles. In contrast, chlorothalonil non-monotonically reduced Bd growth in culture and on tadpoles, with low and high concentrations causing significantly greater mortality than intermediate concentrations and controls. This study is one of only a handful of studies to document a non-monotonic dose response of an invertebrate (Bd) to a pesticide. Although both pesticides reduced Bd growth on tadpoles and in culture, neither eliminated Bd entirely, and because we know little about the long-term effects of the pesticides on hosts (e.g., immunosuppression), I do not recommend using these chemicals to control Bd. In my fourth research chapter, I investigated whether there are non-amphibian hosts for Bd. Non-amphibian hosts could explain how Bd is able to persist in the environment after amphibians are extirpated, and the extreme virulence and distribution of Bd. In laboratory and field studies, I found that crayfish, but not mosquitofish, were hosts for Bd. I found that crayfish could be infected with Bd, could maintain that infection long term (at least 3 months) and could transfer that infection to susceptible amphibians. I also revealed that exposure to water that previously held Bd caused significant crayfish mortality and gill recession, suggesting that Bd releases a chemical that can cause host pathology in the absence of infection. Most efforts to conserve and restore amphibian populations challenged by Bd have been unsuccessful, but managing alternative hosts offers a new and potentially more effective approach to managing Bd. Likewise, identifying the specific pathology-inducing chemical released by Bd might facilitate the development of new strategies to reduce the risk posed by this pathogen. The fifth and sixth research chapters are aimed to improve the quality and efficiency of Bd research. During amphibian development, Bd infections transition from the mouthparts of tadpoles to the skin of post-metamorphic frogs but this transition has never been quantified and thus researchers might be sampling the wrong parts of amphibian bodies to detect Bd. I showed that Bd abundance in O. septentrionalis mouthparts declined from Gosner stages 35-42 and increased on epidermis from Gosner stages 38-46. Assuming our findings are general across species, I recommend sampling mouthparts of amphibians less than Gosner stage 41 and hind limbs of amphibians greater than Gosner stage 41. This should provide researchers with guidance on where to sample to maximize detection of Bd. I also investigated whether Trypan blue dye could be used to determine the viability of Bd. I showed that the proportion of zoospores stained with Trypan blue dye matched the proportion of known dead zoospores added to cultures. In contrast, all of the zoosporangia stage (including known dead zoosporangia) of Bd stained blue. These results demonstrate that Trypan blue can be used to determine the viability of Bd zoospores but not zoosporangia. I recommend using Trypan blue to report the number of live zoospores to which hosts are exposed and to help determine whether factors have lethal or sublethal effects on Bd. My work demonstrates that managing exposure to contaminants and biological reservoirs for Bd might provide new hope for imperiled amphibians. Further exploring how pesticides and pathogens are contributing to amphibian declines will allow us to formulate crucial management and conservation plans to begin remediation.

The sudden appearance of chytridiomycosis, as the cause of amphibian deaths and population declines in several continents suggests that its etiological agent, the amphibian chytrid fungus Batrachochytrium dendrobatidis, was introduced into the affected regions. However, the origin of this virulent pathogen is unknown. Efforts were directed to determine the occurrence of chytridiomycosis in Africa, whether the disease had been introduced into South Africa in recent years and how wild frog populations were affected by infection. A chytridiomycosis survey of 2,300 archived and live specimens involving members of the Pipidae family in sub-Saharan Africa, as well as a number of unrelated frog species in South Africa was conducted by histological diagnosis of skin samples. The epidemiological evidence indicated that chytridiomycosis has been a stable endemic infection in southern Africa for 23 years before any positive specimens were found outside Africa. The occurrence of chytridiomycosis in South Africa can be described as widespread both in terms of geographical distribution and host species and generally infection is not associated with adverse effects at the individual or population level. It was proposed that the amphibian chytrid originated in Africa and that the international trade in the African clawed toad Xenopus laevis that commenced in the mid 1930s was the means of dissemination. A risk assessment of the X. laevis trade demonstrated that chytridiomycosis could spread through this pathway and culminated in the development of a management protocol to reduce the risks of spreading disease through this animate commodity. Initial comparative genetic analysis of B. dendrobatidis strains isolated from South African frogs with a global set of 35 strains, suggests that analysis of a more geographically diverse set of southern African strains is needed before this line of argument can support or reject the "out of Africa" hypothesis. / Thesis (Ph.D. (Zoology))--North-West University, Potchefstroom Campus, 2005.

The Coeur d’Alene salamander (Plethodon idahoensis) is a species of special concern throughout its global range, which includes southeastern BC (COSEWIC, Nov 2007), Idaho, and Montana, due to disjunct populations and sensitivity to human disturbance. Within the Interior Cedar-Hemlock forest on Mount Revelstoke, BC, Coeur d’Alene salamanders occur at their highest abundance between 600 m and 800 m. Beyond the Mount Revelstoke National Park boundaries, the low-order stream habitat of this species is subject to disturbance from forestry, mining, road building, road maintenance, and watercourse diversions such as run-of-the-river hydro projects. We conducted nocturnal salamander surveys and assessed habitat characteristics on 12 Sites (750 m² – 1000 m² stream transects) along three streams from June through September 2006. Coeur d’Alene salamanders were detected from 600 m - 1000 m on seven of the 12 study sites. Relative abundance of Coeur d’Alene salamanders ranged from 0.005 ± 0.001 per m² to 0.025 ± 0.005 per m² on six sites below 950 m. Coeur d’Alene salamanders occurred at an average of 0.001 ± 0.001 per m² at 972 m, the only site above 950 m where we detected salamanders. Our capture-mark-recapture efforts of three surveys per month in June and August yielded a very low recapture rate (3.95 %). Coeur d’Alene salamanders are challenging to enumerate due to their vertical distribution within the soil and underlying geological material. Neonate, juvenile, and adult Coeur d’Alene salamanders were observed from June to September and the highest proportion of neonates occurred in June, soon after the salamanders emerged from winter hibernation. Results of a logistic regression analysis of 1-m² plots reflected the importance of fine scale habitat characteristics (quadrat gradient, boulder, cobble, moss, grass, and shrub) in addition to site-level habitat features (water volume and elevation) that in combination describe the association of Coeur d’Alene salamanders with cool and moist conditions. Coeur d’Alene salamanders appear to select streambed habitat during warm, dry periods, which may be a behavioural response to minimize dehydration during periods of activity at the surface of the forest floor.

This study examined the effects of temperature and chronic hypoxia (CH) on pH/CO2- sensitive fictive breathing, and central pH/CO2 chemosensitivity, in cane toads (Bufo marinus). Toads were exposed to CH (10% or 15% O2) or control conditions (21% O2) for 10 days at either room temperature (controls), 10°C or 30°C following which in vitro brainstem-spinal cord preparations were used to examine central pH/CO2-sensitive fictive breathing (i.e., motor output from respiratory nerves which is the neural correlate of breathing). A reduction in artificial cerebral spinal fluid (aCSF) pH increased fictive breathing frequency (fR) and total fictive ventilation (TFV). Cold temperature reduced and hot temperature increased fR and TFV under control conditions. CH attenuated fictive breathing independently of temperature. Additional experiments in which the aCSF temperature was varied indicate that the effects of temperature acclimation result from neural plastic changes within respiratory control centres in the brain.

No description available.

Salamanders are critical components of forest ecosystems, in terms of total biomass, as well as for their value as indicators of ecosystem stress. Considering the worldwide decline in amphibian populations, the known effects of timber harvest on salamander populations, and the importance of the forest products industry in Kentucky and elsewhere, the impacts of silvicultural operations on salamander communities cannot be overlooked. The objective was to investigate the effects of three different silvicultural treatments, each involving different streamside management zone (SMZ) characteristics, on salamander communities in ephemeral streams. Data were collected by regular checks of pitfall traps, coverboards, and transect searches. Using both pre- and post-harvest data, abundance estimates were acquired using binomial mixture models. Declines in some species of terrestrial and stream-breeding salamanders were detected, and were shown to be likely related to characteristics of the corresponding silvicultural treatment. Applying modest SMZ regulations to ephemeral streams would likely alleviate these declines significantly.