Experimental examination of the effects of ultraviolet-B radiation in combination with other stressors on frog larvae
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- Searle, C.L., Belden, L.K., Bancroft, B.A. et al. Oecologia (2010) 162: 237. doi:10.1007/s00442-009-1440-8
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Ultraviolet-B radiation (UVB) is a ubiquitous stressor with negative effects on many aquatic organisms. In amphibians, ambient levels of UVB can result in impaired growth, slowed development, malformations, altered behavior and mortality. UVB can also interact with other environmental stressors to amplify these negative effects on individuals. In outdoor mesocosm and laboratory experiments we studied potential synergistic effects of UVB, a pathogenic fungus, Batrachochytrium dendrobatidis (Bd), and varying temperatures on larval Cascades frogs (Rana cascadae). First, we compared survivorship, growth and development in two mesocosm experiments with UVB- and Bd-exposure treatments. We then investigated the effects of UVB on larvae in the laboratory under two temperature regimes, monitoring survival and behavior. We found reduced survival of R. cascadae larvae with exposure to UVB radiation in all experiments. In the mesocosm experiments, growth and development were not affected in either treatment, and no effect of Bd was found. In the laboratory experiment, larvae exposed to UVB demonstrated decreased activity levels. We also found a trend towards reduced survival when UVB and cold temperatures were combined. Our results show that amphibian larvae can suffer both lethal and sublethal effects when exposed to UVB radiation.
KeywordsRana cascadaeBatrachochytrium dendrobatidisTemperatureUVB
In the past 50 years, humans have altered ecosystems more rapidly than during any other time in history (Millennium Ecosystem Assessment 2005) creating environmental conditions that threaten many ecosystems. For example, recent anthropogenic emissions into the atmosphere have reduced stratospheric ozone from historic levels. This depletion of the ozone layer allows more harmful ultraviolet-B radiation (UVB; 280–315 nm) to reach the earth’s surface. While the success of the 1987 Montreal Protocol on Substances that Deplete the Ozone Layer has greatly reduced the production of ozone-depleting chemicals (Solomon 2004), some estimates suggest that full recovery is not expected to occur until 2068 (Newman et al. 2006). Thus, the impacts of increased UVB exposure will continue for some time.
In aquatic systems, exposure to UVB can kill sensitive organisms or induce sublethal effects (Bancroft et al. 2007; Häder et al. 2007) that could potentially have large impacts on populations. In addition to population effects, UVB can profoundly affect community structure in experimental aquatic systems (Chatila et al. 1999; Danilov and Ekelund 2000). For example, Danilov and Ekelund (2000) found that marine epilithic communities dominated by diatoms in microcosms quickly shifted to a community dominated by cyanobacteria after only 7 days’ exposure to UVB radiation. Another example is that of Bothwell et al. (1994) who showed that greater amounts of algae accumulate in UV-exposed habitats than in UV-protected environments. UVB radiation inhibits algal consumers (Diptera: Chironomidae) since larval chironomids are more sensitive to UVB than sympatric algae. Differential sensitivity to UVB between algae and herbivores contributes to counterintuitive increases in algae in habitats exposed to UVB.
The ubiquitous nature of UVB radiation may result in wide-reaching effects on many organisms. Amphibians are one group of organisms for which there are well-documented negative effects of exposure to ambient levels of UVB radiation (reviewed in Croteau et al. 2008). UVB exposure in amphibians can reduce hatching success (e.g., Lizana and Pedraza 1998; Häkkinen et al. 2001), cause developmental and physiological deformities (e.g., Hays et al. 1996; Starnes et al. 2000; Pahkala et al. 2001; Ankley et al. 2002), alter growth rates (e.g., Smith et al. 2000; Pahkala et al. 2003a, b), increase pigmentation (Langhelle et al. 1999), alter behavior (e.g., Kats et al. 2000) and decrease survival (e.g., Nagl and Hofer 1997; Tietge et al. 2001; Blaustein et al. 2005a). However, these effects are species specific, vary with life history stage, and may be context dependent.
Many studies of the effects of UVB exposure have focused on amphibian embryos assuming them to be the most susceptible life stage. However, a recent meta-analysis by Bancroft et al. (2008a) demonstrates that amphibian larvae are more sensitive to UVB exposure than embryos. Limited data on the effects of UVB radiation on post-hatching stages of amphibians have restricted our ability to ascertain the overall importance of UVB on amphibian populations. Mortality at post-hatching stages may impact the population more significantly than mortality at the embryonic stage (Vonesh and De la Cruz 2002). Therefore, understanding the effects of UVB on amphibian larvae is an important step in understanding population-level processes.
Although exposure to UVB radiation alone can be harmful to amphibians, it may be especially harmful in combination with other stressors. Pollutants (e.g., Hatch and Blaustein 2003; Macías et al. 2007), pathogens (e.g., Kiesecker and Blaustein 1995), and low pH (e.g., Long et al. 1995; Pahkala et al. 2002), can enhance the toxic effects of UVB exposure. Additionally, UVB radiation may increase the negative effects of other stressors. For example, exposure to ambient UVB radiation can increase the occurrence and pathogenic effects of an oomycete (Saprolegnia ferax) in amphibian embryos (Kiesecker and Blaustein 1995). Complex interactions involving El Niño events and exposure to UVB radiation may influence the emergence of this pathogen (Kiesecker et al. 2001). Exposure to UVB radiation may make hosts more susceptible to pathogens by compromising immune systems or inducing other stress effects (Tevini 1993). While pathogens and UVB can interact to impact amphibian embryonic development and survival, no studies have examined this interaction in larvae. This is surprising because amphibian larvae are hosts to several emerging pathogens such as water molds (Kiesecker and Blaustein 1995), trematode parasites (Johnson et al. 2002) and the fungus, Batrachochytrium dendrobatidis (Bd: Longcore et al. 1999), and the forces stimulating the emergence of these pathogens are unknown.
Bd is an emerging infectious pathogen associated with mass mortality events of amphibians around the world (Lips et al. 2006; Rachowicz et al. 2006; Skerratt et al. 2007). It affects both larval and metamorphosed amphibians by infecting their mouthparts and keratinized epidermal cells, respectively (Longcore et al. 1999; Piotrowski et al. 2004). Infection by Bd can kill larvae and post-metamorphic stages of amphibians (Berger et al. 2005; Blaustein et al. 2005b; Carey et al. 2006) and can cause sublethal damage (Parris and Cornelius 2004). Susceptibility to Bd may be context dependent where changes in temperature (Andre et al. 2008), exposure to water contaminants (Parris and Baud 2004), climate change (Pounds et al. 2006; Bosch et al. 2007), differences in host species (Blaustein et al. 2005b) and differences in Bd strain (Berger et al. 2005) may alter host-pathogen dynamics. Thus, the combined detrimental effects of both Bd and UVB radiation on amphibian larvae may not be as straightforward as the effects of either stressor acting alone. There have been no investigations of the combined effects of UVB and Bd on larval amphibians which are important in understanding disease dynamics in amphibian populations.
UVB effects on amphibians can also be influenced by abiotic factors such as temperature. Van Uitregt et al. (2007) show an increase in the negative effects of UVB when the embryos and larvae of one species of amphibian are exposed to colder temperatures. If this occurs in other species, larvae in colder habitats or larvae that choose colder temperatures may be at greater risk than those in warmer temperatures. However, many amphibians seek warmer temperatures (Lucas and Reynolds 1967; Brattstrom 1979; Dupré and Petranka 1985; Wollmuth et al. 1987) to speed their development. Warmer temperatures preferred by amphibian larvae are often located in shallow areas of aquatic habitats where levels of UVB are higher (Kirk 1994; Bancroft et al. 2008b). Thus, larval preference to choose warmer temperatures may also expose them to higher levels of UVB, and this temperature choice may influence the degree to which they are affected.
We conducted a series of experiments to examine the combined effects of UVB radiation and Bd infection, and the combined effects of UVB and temperature on the larvae of Cascades frogs (Rana cascadae). R. cascadae are found in the Cascade Mountains of the Pacific Northwest, USA, where they serve an important ecological role as herbivores at the larval stage and carnivores as adults (Jones et al. 2005). Population declines of R. cascadae have been observed in some parts of their range (Jones et al. 2005). In nature, R. cascadae are continually exposed to a combination of UVB radiation (Blaustein et al. 1994), pathogens (Kiesecker and Blaustein 1995; Fellers et al. 2008) and other biotic and abiotic stressors. Exposure of R. cascadae to UVB radiation as embryos decreased hatching success (Blaustein et al. 1994), and as larvae reduced survival (Belden et al. 2003), decreased growth, and increased deformities (Romansic et al. 2009). In laboratory experiments, juvenile R. cascadae show reduced survival when exposed to Bd (Garcia et al. 2006). In the only experimental study of the effects of Bd on larval R. cascadae, Bd-exposed individuals had malformed mouthparts but did not show greater mortality than control larvae (Blaustein et al. 2005b). These stressors have been examined in isolation, but it is unclear if they have synergistic effects on R. cascadae.
Because of the sensitivity of R. cascadae to both UVB radiation and Bd, we hypothesized that Bd and UVB may act synergistically to harm R. cascadae larvae. To test this hypothesis, we performed experiments in outdoor mesocosms. Outdoor mesocosms allow animals to be exposed to natural changes in light and temperature to best mimic natural conditions. In addition, we performed a laboratory experiment where we artificially controlled temperature and UVB to determine how temperature interacts with UVB to affect survival and activity in R. cascadae larvae.
Materials and methods
We collected R. cascadae as larvae (mesocosm experiment 1) or embryos (mesocosm experiment 2 and the laboratory experiment) and reared them in the laboratory in 37.8-l aquaria filled with dechlorinated water. As embryos, animals were maintained with one egg mass per aquarium. Larvae were kept at a density of approximately 200 animals per aquarium and fed a mixture of ground rabbit chow and Tetramin fish food (3:1 ratio by volume). Animals were given weekly water changes in a controlled laboratory environment with a 12:12-h light:dark photoperiod at 14.5–15.5°C.
Mesocosm experiment 1
This experiment was conducted from 12 September to 19 November. It consisted of a 2 × 3 design with larvae exposed to two levels of UVB radiation [shielded and exposed (ambient)] and three levels of Bd (strain JEL197, strain JEL215, and unexposed control) conducted in outdoor mesocosms near Corvallis (Benton County, Oregon; elevation: 71 m). Each treatment was replicated in five randomly assigned mesocosms. We filled 30 mesocosms (1.9 m in diameter) with water to a depth of 52 cm to contain ~368 l of water. Into each mesocosm, we added dried leaves, phytoplankton, rabbit chow, and zooplankton to mimic a natural environment. Mesocosms were left undisturbed for 2 weeks prior to the addition of larvae and application of treatments to allow phytoplankton and zooplankton to establish. At the beginning of the experiment, we measured nitrate (<2 mg/l), dissolved oxygen (6.4–8.4 mg/l), and pH (6.2–6.8) of the mesocosm water.
R. cascadae larvae were collected from Potholes wetland (Deschutes County, Oregon; elevation: 2,300 m) in August 2000. Eight larvae [Gosner (1960) stages 29–39] were randomly assigned and added to each of the 30 mesocosms. We controlled UVB exposure by covering mesocosms with transparent plastic filters that either shield or transmit UVB (mylar and acetate, respectively, 0.127 mm thickness; Hillcor Plastics). Mylar filters transmit 5% of ambient UVB radiation while acetate filters transmit 80% of ambient UVB radiation though both allow equal levels of other wavelengths to pass through (Blaustein et al. 1994). Filters were attached to the top of each mesocosm. Temperature loggers were placed in three UVB-shielded and three UVB-exposed mesocosms to record water temperature every 6 h for the duration of the experiment. Temperatures in the mesocosms ranged from 1 to 27°C during the experiment.
Bd was cultured in the laboratory using a standard protocol (Longcore et al. 1999). One day after adding larvae into the mesocosms, we added a single 10-cm Petri dish containing JEL197, JEL215 or a Bd-free control of nutrient agar to each mesocosm. Upon visual confirmation of zoospores using a light microscope, each Petri dish was flooded with 3 ml of mesocosm water and allowed to sit for 3 min to allow zoospores to discharge from zoosporangia (Longcore et al. 1999). After 3 min, 0.5 ml of the zoospore suspension was collected and analyzed under a hemocytometer to estimate zoospore density of each dish. Petri dishes were then placed in mesh bags approximately 2 cm beneath the surface of the mesocosm water and attached to the sides of the mesocosms with metal clips. Water samples were collected from the mesocosms for the following 2 days and observed under a light microscope to estimate zoospore densities in the mesocosms.
Three weeks after the addition of larvae to the mesocosms, we counted the number of larvae in each mesocosm to determine larval mortality (percent survival at week 3). We also collected a subsample of three larvae from each mesocosm, which were sent to the Zoological Society of San Diego to determine presence of Bd infection in mouthparts through histological examination.
During the experiment, any larva reaching metamorphosis [Gosner (1960) stage 43] was removed and recorded (time to metamorphosis). To determine if treatments had a carry-over effect into post-metamorphic stages, we fed and maintained these animals in the laboratory for 30 days post-metamorphosis to observe survivorship. These animals were placed in individual 15-cm Petri dishes with moistened paper towels at 14.5–15.5°C. Paper towels were changed once a week and animals were fed pinhead crickets approximately twice a week. After 30 days in the laboratory, animals were euthanized in MS-222 and preserved in 70% ethanol.
Survival to week 3, time to metamorphosis, and survival at 30 days past metamorphosis were analyzed with a generalized linear mixed model implemented in R statistical software environment. Mortality data were analyzed using a logit link while time to metamorphosis used an identity link. We nested individuals by mesocosm and tested UVB effects, Bd effects and the interaction of the two variables.
Mesocosm experiment 2
This experiment was conducted from 14 July to 31 July. Mesocosm experiment 2 differs from experiment 1 by using a different strain of Bd (JEL274), modifying the inoculation method, and increasing our sample size (in the number of mesocosms and the number of larvae per mesocosm). This experiment is also shorter in duration than mesocosm experiment 1 to determine the short-term effects of UVB and Bd exposure. We used a 2 × 2 design with two levels of UVB [shielded and exposed (ambient)] and two levels of Bd (strain JEL274, and unexposed control). Each treatment was replicated in six randomly chosen mesocosms. Mesocosms were filled as described for experiment 1 and left for 3 weeks before initiation of the experiment. We placed a temperature logger into three UVB-shielded and three UVB-exposed mesocosms to record temperature every hour. Temperatures in the mesocosm ranged from 19.1 to 34.2°C.
We created UVB-exposed and UVB-shielded treatments using filters as described in experiment 1. UVB levels were measured using a hand-held Solar Light meter with a UVB attachment (PMA21100 meter, 2102 probe; Solar Light, Philadelphia, Pa.) every 5 days between 1100 and 1300 hours. Ambient UVB levels at midday ranged from 16.6 to 19.4 μW/cm2. Mesocosms covered with mylar had UVB levels from 1.3 to 1.9 μW/cm2 at the top of mesocosm water, attenuating to 0.1–0.5 μW/cm2 at 10 cm below the water’s surface. Mesocosms covered with acetate had UVB levels ranging from 9.6 to 13.5 μW/cm2 at the top of mesocosm water, attenuating to 0.3–2.0 μW/cm2 at 10 cm below the water’s surface.
In June 2006, three egg masses of R. cascadae and three egg masses of Pacific treefrogs (Psuedacris regilla) were collected from Susan’s pond (Deschutes County, Oregon; elevation: 1,954 m). We applied Bd treatments by placing either Bd-exposed or Bd-control P. regilla larvae into the mesocosms. Therefore, P. regilla acted as our stimulus animals while R. cascadae remained our focal animals. To inoculate P. regilla larvae, we divided them into six 37.8-l aquaria with approximately 80 animals per aquarium and each aquarium was randomly assigned to Bd or control treatments. We used eight Petri dishes containing Bd strain JEL274 to inoculate the P. regilla in each Bd aquaria and eight sterile agar dishes for each control aquaria. Each dish was flooded with 15 ml distilled water for 20 min and this wash was then poured into the aquaria. Three additional Bd dishes were flooded in the same manner and wash was used to determine zoospore densities on a hemocytometer. Stimulus Bd treatment P. regilla larvae were exposed to an average of 1,020 zoospores of Bd per liter in their exposure aquaria. Similar methods have been shown to successfully infect both larval amphibians and adults (Berger et al. 2005; Blaustein et al. 2005b; Carey et al. 2006; Han et al. 2008). We allowed Bd infection to develop for 3 weeks after inoculation before using the P. regilla in our experiment.
On 13 July, we added ten R. cascadae larvae [Gosner (1960) stage 24–25] into each mesocosm. The following day, 12 P. regilla larvae [Gosner (1960) stage 25–27] confined within mesh bags were added to each mesocosm. Control mesocosms were given 12 unexposed P. regilla while Bd mesocosms were given 12 Bd-exposed P. regilla. Because Bd is transmitted through water (Longcore et al. 1999), infected P. regilla can shed zoospores that pass out of the bags to infect the R. cascadae. After 18 days, all animals were euthanized in MS-222 and preserved in 70% ethanol. Length (snout-vent) and weight were measured for each animal. To test for Bd infection, we randomly selected three R. cascadae from each mesocosm (if three animals were available) to analyze with quantitative-polymerase chain reaction (qPCR). Additionally, six randomly chosen P. regilla were also tested for Bd infection using qPCR. Mouthparts were removed from each animal and DNA was extracted using Prepman Ultra (Applied Biosystems) methods described by Boyle et al. (2004). Extractions were diluted to a 10% solution. Using the methods described by Boyle et al. (2004), we performed qPCR on each sample using an ABI PRISM 7500 sequence detection system. Each sample was run in triplicate and any value above 0.1 genome equivalents was considered to show infection.
Length, weight, and survival data were analyzed as described in mesocosm experiment 1. In one UVB-shielded, Bd-exposed mesocosm, P. regilla larvae escaped from their mesh bags so this mesocosm was excluded from analysis.
To examine the combined effect of UVB radiation and temperature on larvae, we used a 2 × 2 design in a controlled laboratory environment with two levels of UVB (shielded and exposed) and two levels of temperature (hot and cold). Twenty water baths were created and randomly assigned a hot or cold treatment. An aquarium heater was placed into the center of each hot treatment bath and turned on at 0900 hours and off at 1700 hours each day. This created an increase in water temperature during the middle of the day in the hot treatments, and a return to similar temperatures as the cold treatments at night. Into each water bath, we placed six 1-l containers filled with 800 ml of dechlorinated water to a depth of 11.5 cm. A digital thermometer (Traceable Thermometer; Fisher Scientific) was used to measure temperature every 2 h at the center of the water bath. Containers in the cold water baths averaged low temperatures of 15.2°C (SD = 0.46) and high temperatures of 16.0°C (SD = 0.60) throughout the day. Containers in the hot treatments averaged low temperatures of 15.6°C (SD = 0.36) and high temperatures of 30.5°C (SD = 1.87). Temperatures within the water baths are shown in Fig. S1 (electronic supplementary material).
Animals from six egg masses of R. cascadae were collected from Parish pond (Linn County, Oregon; elevation: 1,130 m) in April, 2007. One larva [Gosner (1960) stages 25–26] was added to each container. UV-B treatments were applied by placing larvae under a mixture of UVB (Q-Panel UVB 313; Q-Panel, Cleveland, Ohio) and full-spectrum bulbs (Vita-Light; Durotest, Fairfield, N.J.). Lights were turned on from 0800 to 1800 hours each day. In each water bath, three animals were randomly assigned a UVB-exposure treatment and three were assigned a UVB-shielded treatment. Treatments were applied by covering each container with either a mylar or acetate filter as in the previous experiments. UVB levels at the top of the water below acetate filters ranged from 11.8 to 15.7 μW/cm2, whereas UVB levels below mylar filters ranged from 0.2 to 0.7 μW/cm2. These are within UVB levels found in the Cascade Mountains, where R. cascadae naturally occur (Bancroft et al. 2008b).
Treatments were applied for 5 consecutive days. Each day, the containers within each water bath were randomly rearranged to remove possible effects of orientation. At 1800 hours on day 5, survival was recorded for all individuals. Fourteen surviving individuals from each treatment were randomly chosen as a subsample of animals for a behavior trial measuring activity levels. Activity levels are closely associated with growth rates, which are extremely important for development to metamorphosis (Werner and Anholt 1993). Thus, if UVB or temperature treatments influence larval activity, this could have profound effects on individuals. The behavior trial was conducted from 0900 to 1300 hours on day 6 after allowing treatments to acclimate overnight to the behavioral arena’s temperature of 15°C. Each larva was placed into a plastic container (20 cm long by 30 cm wide) filled with water to a depth of 5 cm over a grid containing 5 × 5-cm squares. Containers were placed randomly within an observation arena surrounded by black sheets with small openings to allow observers to record tadpole movement without disturbing the animals. After a 1-h acclimation period in the new containers, activity levels were recorded by counting the number of lines crossed by each animal over a total of 4 min. Two observers recorded activity levels of each larva 8 times for 30 s with 30 min between observations.
We analyzed both survival and behavior using generalized linear mixed models to determine the effects of UVB, temperature and the interaction of the two variables. Survival was analyzed with a logit link function while activity levels used an identity link. Individuals were nested by water bath.
Mesocosm experiment 1
Mesocosm experiment 2
Exposure to ambient levels of UVB radiation reduced survival in larval R. cascadae. In all experiments, R. cascadae exposed to UVB radiation had significantly lower survival than those shielded from UVB. This is one of the few experimental studies to unequivocally demonstrate mortality of amphibian larvae when exposed to ambient levels of UVB radiation (Nagl and Hofer 1997; Tietge et al. 2001; Belden et al. 2003).
Furthermore, in our mesocosm experiments, larvae were exposed to ambient levels of UVB radiation in a close approximation of natural habitat (O’Hara and Blaustein 1985; Hokit and Blaustein 1997). Reduced survival in these conditions suggests that UVB exposure can cause mortality of amphibian larvae in the wild. In mesocosms, as in many natural habitats, larvae had the opportunity to behaviorally reduce their UVB exposure by choosing deeper waters or hiding under leaves. While we did not directly record behavior, we often observed R. cascadae larvae near the surface of the mesocosm water where UVB levels were highest. Additionally, mortality in the UVB-exposed treatments suggests that animals did not behaviorally limit their exposure to UVB radiation. This adds to the growing evidence that some species of larval amphibians do not behaviorally avoid UVB radiation, even when it causes them harm (Wollmuth et al. 1987; van de Mortel and Buttemer 1998; Belden et al. 2003; Bancroft et al. 2008b).
Direct comparisons between the mesocosm experiments cannot be made; however, overall survival in mesocosm experiment 1 was much greater than survival in mesocosm experiment 2. These differences could be explained in a number of ways. For example, the experiments were conducted in different years, different months, for different durations and with different protocols. Also, larvae in mesocosm experiment 2 were exposed at earlier developmental stages than those in the first mesocosm experiment. However, UVB exposure increased mortality in both mesocosm experiments.
Although we exposed our animals to Bd in mesocosm experiments, no effect of Bd was found. In experiment 1, animals did not show signs of Bd infection, even though appropriate levels for infection (Carey et al. 2006) were found inside the mesocosm water. It is possible that under our conditions the virulence of Bd was compromised. This could be due to a number of factors including competition with other microorganisms in the mesocosm, changes in temperature or the relative resistance of the host species. Another possibility is that larvae may have carried low levels of Bd infection that were undetectable by histological examination in mesocosm experiment 1. In experiment 2, temperatures in the mesocosms reached over 30°C for 8 consecutive days (experimental days 7–14) which is high enough to kill Bd in culture (Piotrowski et al. 2004). Therefore, our negative qPCR results may demonstrate the ability of high temperatures to cure Bd infection in aquatic systems (Woodhams et al. 2003). R. cascadae were exposed to Bd in the first 6 days of the experiment, but previous studies by Blaustein et al. (2005b) found no mortality of R. cascadae larvae with exposure to Bd, so this species may not be susceptible to Bd infection at this life stage. In a study on juvenile R. cascadae, Garcia et al. (2006) tested the combined effects of UVB radiation and Bd, and found increased mortality with exposure to Bd, but no UVB effect or interaction between treatments. However, Bd infection can vary greatly between life stages due to changes in keratinized structures. While larval amphibians are only infected in their mouthparts, juveniles have keratinized epidermal tissue which makes them susceptible to infection over most of their skin. Varying responses to the separate and combined effects of UVB and Bd infection between life stages of R. cascadae highlights the complexity underlying amphibian population declines.
In the laboratory, we found both lethal and sublethal effects on R. cascadae when exposed to UVB radiation. While lethal effects can dramatically alter populations, sublethal effects such as reduced activity can also have a substantial impact on larvae in the wild. Reduced activity levels can decrease feeding rates and lead to smaller size at metamorphosis (Skelly and Werner 1990). Lower activity levels may prevent predators from finding larvae (Werner and Anholt 1993), but if pursued by a predator, lethargic larvae may be unable to escape. Therefore, these sublethal effects of UVB may indirectly reduce larval survival and thus reduce population size.
Additionally, we found reduced survival of animals exposed to UVB radiation in colder temperatures. This complements the findings of van Uitregt et al. (2007) who observed similar trends with reduced survival, growth and performance when striped marsh frog (Limnodynastes peronii) larvae were exposed to UVB at colder temperatures. Cold temperatures could increase the negative effects of UVB by physiologically reducing a larva’s ability to prevent damage caused by UVB. For example, repair enzymes are essential in fixing DNA damage caused by UVB radiation (Pang and Hays 1991). These enzymes work faster at warmer temperatures, so cold conditions may slow an organism’s ability to recover after exposure to UVB. Additionally, changes in temperature may influence larval behavior and therefore alter their exposure to UVB radiation. Amphibian larvae at high elevations are exposed to high levels of UVB and colder conditions compared to those at lower elevations. This combination of environmental factors may act together and could contribute to amphibian population declines at high elevations. UVB can cause mortality in cold temperatures, but even surviving animals may have a decreased ability to cope with additional stressors. Therefore, any UVB-sensitive species occurring in cold climates may be at risk. However, within a habitat, many larval amphibians choose regions with warmer temperatures. While larval preference for warmer temperatures may help mitigate the effects of UVB, warmer regions of water bodies often have higher levels of UVB. Therefore, larval amphibians are forced to choose between high levels of UVB in warm conditions where they are more able to prevent negative effects of UVB, or lower levels of UVB in cold regions where they are less able to cope with UVB. This complicated pattern makes it difficult to predict the threat of UVB in larval amphibians in the wild.
Our study shows that larval amphibians can suffer both lethal and sublethal negative effects of UVB radiation. Future work should continue to investigate the impacts of UVB on amphibian populations by studying all life stages to fully understand its effects on populations. While we did not directly study the effects of UVB at the population level, our results suggest that UVB radiation can impact R. cascadae at a life stage that is critical to amphibian populations (Vonesh and De la Cruz 2002). Therefore, investigating only the embryonic or adult stages may underestimate the negative effects of UVB. The cumulative effects of embryonic, larval and adult mortality from UVB could have larger impacts on populations than predicted by studying one stage alone. The ubiquitous increase of UVB radiation across the globe makes it a potentially major factor contributing to amphibian declines. Therefore, future work should focus on the effects of UVB in order to better understand how degradation of the ozone layer has affected, and continues to affect, aquatic organisms.
We would like to thank A. Pessier, J. Spatafora, J. Romansic, J. Longcore, T. Raffel, P. Bradley, A. Searle, J. Carey, and M. Christie for their assistance. This work was supported by National Science Foundation Integrated Research Challenges in Environmental Biology (NSF IRCEB) Program (DEB0213851 and IBN9977063). Suggestions by two anonymous reviewers greatly contributed to this paper. These experiments comply with the current laws of the United States and with Oregon State University animal care regulations. Animals were collected according to Oregon Department of Fish and Wildlife regulations.