Contrasting effects of ultraviolet radiation on the growth efficiency of freshwater bacteria
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In this study, we tested the hypothesis that the growth efficiency of freshwater bacteria is differentially affected by ultraviolet radiation (UVR, 280–400 nm) as mediated through changes in their production and respiration rates. Five bacterial strains affiliated to Alphaproteobacteria, Betaproteobacteria, Gammaproteobacteria, and Actinobacteria were isolated from different freshwater habitats and exposed in the laboratory to photosynthetically active radiation (PAR) and PAR + UVR, or kept in the dark for 4 h. Afterward, bacterial carbon production and respiration were assessed by measuring leucine incorporation and oxygen consumption rates, respectively. Ultraviolet radiation decreased significantly the bacterial production of Acidovorax sp., Pseudomonas sp. and Actinobacterium MHWTa3, and the respiration rate of Acidovorax sp. and Acinetobacter lwoffii. Measurements of respiration of a natural bacterial community collected from the same lake where A. lwoffii was isolated resulted in significantly higher rates after exposure to PAR + UVR than in the dark. In the presence of UVR, bacterial growth efficiency significantly decreased in Acidovorax sp., Pseudomonas sp., and Actinobacterium MHWTa3, but it increased in A. lwoffii or it remained unchanged in Sphingomonas sp. Our results indicate that although the outcome was strain-specific, UVR has the potential to alter the efficiency by which dissolved organic matter is transformed into bacterial biomass and thus to affect the biogeochemical carbon cycle.
KeywordsBacterial respiration Bacterial production Sphingomonas Acinetobacter Actinobacterium Alpine lakes
Heterotrophic bacteria are a key component in the biogeochemical carbon cycle of aquatic ecosystems. The bacterial community is responsible for the remineralization of the dissolved organic matter (DOM) pool, which leads to the production of new bacterial biomass and also to the oxidation of this reduced organic carbon pool to inorganic carbon that is released into the atmosphere through bacterial respiration. The balance between these metabolic processes can be assessed by calculating the bacterial growth efficiency, a parameter that reflects the efficiency of heterotrophic bacteria in converting organic carbon into bacterial cellular carbon (del Giorgio and Cole 1998). The accurate estimation of bacterial growth efficiency in natural communities is far from being trivial although it is the basis to understand ecosystem functioning.
Bacterial production is measured by following the incorporation rates of radiolabeled thymidine (Fuhrman and Azam 1980) or leucine (Kirchman et al. 1985) into bacterial deoxyribonucleic acid and proteins, respectively. A recent study, however, has cautioned on the use of thymidine for the measurements of bacterial production in lakes because a significant fraction of the Betaproteobacteria is not able to taken up this substrate (Pérez et al. 2010). To estimate the produced bacterial biomass, incorporation rates are transformed either by theoretical or by empirical conversion factors, which are however highly variable across aquatic systems (Biddanda et al. 1994; Buesing and Marxsen 2005). Bacterial respiration can be estimated by measuring oxygen consumption or CO2 production rates, and likewise important as for the assessment of bacterial production, incubation times should be kept as short as possible to minimize changes in bacterial community composition (Gattuso et al. 2002). For example, this can be achieved by using fast-responding microelectrodes for oxygen measurements (Warkentin et al. 2007; Pringault et al. 2009) or by estimating oxygen consumption from electron transport system (ETS) activity (del Giorgio 1992). However, in oligotrophic and cold aquatic ecosystems, incubations are necessarily long and in some cases detection of significant oxygen changes can represent a real challenge.
Besides variations caused by methodological factors, numerous environmental variables could affect the bacterial growth efficiency in natural aquatic ecosystems (del Giorgio and Williams 2005). Among those environmental variables, sunlight is known, for example, to stimulate bacterial production in humic lakes due to the phototransformation of DOM and the consequent increase in the availability of nutrients (Reche et al. 1998). However, this indirect stimulatory effect of sunlight on production is usually not observed in transparent aquatic systems where UV radiation (UVR, 280–400 nm) has usually a negative effect on bacteria (i.e., Chatila et al. 2001; Buma et al. 2003 and references therein). In fact, in UV transparent lakes such as alpine ones, bacterial production in the upper meters of the water column is strongly reduced by UVR (Sommaruga et al. 1997). Solar UVR is known to induce oxidative stress in aquatic bacteria through the production of reactive oxygen species, which in turn damage cell components (Jeffrey et al. 2000; Maranger et al. 2002). Direct negative effects of UVR have been observed on bacterial growth (Sieracki and Sieburth 1986), viability (Helbling et al. 1995), and enzymes production (Herndl et al. 1993; Garde and Gustavson 1999). However, there are large differences in sensitivity to solar UVR among marine bacterial taxa when growth patterns (Agogué et al. 2005), viability (Joux et al. 1999), and activity (Alonso-Sáez et al. 2006) are assessed. Thus, generalizations on the response of bacterial groups or communities to UVR is difficult, because bacteria have evolved diverse protection mechanisms against UV stress such as the synthesis of photoprotective substances (Müller et al. 2005) or have efficient repair processes to minimize UV-induced DNA damage (Boelen et al. 2001; Buma et al. 2003).
Currently, information on how light and particularly UVR affects bacterial growth efficiency is scarce (Pakulski et al. 1998; Pringault et al. 2009), and the studies available have addressed the whole bacterial community of marine ecosystems. Equivalent information on bacterial isolates or in freshwater ecosystems is not available. Further, in some studies bacterial respiration has been estimated indirectly (Hernandez et al. 2007), thus making difficult the direct comparison of results. In this study, we assessed the production and respiration rates of freshwater bacterial isolates kept in darkness or exposed to photosynthetically active radiation (PAR, 400–700 nm) and PAR + UVR and calculated their growth efficiencies. Most of the isolates included in the study are members of different bacterial groups found in alpine lakes (i.e., lakes located above the treeline), which are very oligotrophic and UV transparent (Laurion et al. 2000) or they were included because of its uniqueness regarding cultured members (Hahn et al. 2003). We hypothesized that the effect of UVR on bacterial growth efficiency is strain-specific among freshwater bacteria. In addition, we also tested the effect of PAR + UVR on respiration rates of the natural bacterial community from one of the lakes where the isolates were obtained.
Materials and methods
Sources of bacterial strains
Affiliation, origin, cultivation medium, and growth characteristics of the bacterial isolates tested in this study
Sphingomonas sp. B14
Schwarzsee ob Sölden, AUT
Rain water, Gossenköllesee, AUT
Media used for isolation and cultivation of bacterial strains
For the isolation of bacteria, 0.25 ml of unfiltered water was plated onto solid nutrient broth-soyotone-yeast extract (NSY) medium (Hahn et al. 2003). Isolated single colonies were recultured on solid NSY medium and transferred to liquid NSY several times before being recultured in inorganic basal medium (IBM) (Hahn et al. 2003) supplemented with 2.5 mg glucose l−1 (IBMG). The concentration of dissolved organic carbon (DOC) in IBMG was 1.0 mg l−1. This value was selected as a compromise between being able to detect growth and resembling those DOC concentrations found in the habitats (0.3–0.7 mg l−1, Laurion et al. 2000) from which bacteria were isolated. In addition, glucose has also the advantage that is not photodegraded under the radiation conditions we used in the experiment (i.e., absence of UVC where glucose absorbs) and that bacteria are usually able to transform this sugar into all the necessary amino acids, vitamins, and nucleotides that make up cells (Gottschalk 1986). For the strain MHWTa3 that originates from a very eutrophic lake, NSY medium was used for cultivation and determination of growth curves. Cultivation took place in a walk-in room set at 15 ± 1°C. During cultivation, the isolates were not exposed to UVR, but except for isolate MHWTa3, all the others originate from high UV environments. For example at the depth where bacteria were isolated in Gossenköllesee and Schwarzsee ob Sölden (i.e., 1 m), UVR at 320 nm is still ca. 85 and 70%, respectively, of that measured at the surface (Laurion et al. 2000).
For the isolation of bacterial DNA, 2 ml of bacterial culture was filtered onto polycarbonate white filters (Millipore GTTP, 0.22 μm pore size) and the dried filters were frozen (−20°C) until further processing. DNA was isolated from the filters with a customary DNA isolation kit (PowerSoil Isolation Kit, MO BIO laboratories, CA, USA). PCR amplification of the bacterial 16S rRNA gene was done with the primers 27 forward (5′-AGA GTT TGA TCM TGG CTC AG-3′) (Lane et al. 1985) and 1,492 reverse (5′-TAC GGY TAC CTT GTT ACG ACT T-3′) (Kane et al. 1993) using a HotStarTaq® Plus Master Mix Kit (QIAGEN GmbH, Hilden, Germany) following the manufacturer’s instructions. The thermocycling program consisted of the following steps: initial activation at 95°C for 5 min, 30 cycles of denaturation at 94°C for 1 min, annealing at 52°C for 1 min, extension at 72°C for 2 min, and a final extension step for 10 min at 72°C. Sequencing reactions were done using external facilities (http://www.macrogene.com). To search for related 16S rRNA sequences with high similarity values, the obtained sequences were submitted to the Basic Local Alignment Search Tool (BLAST) (http://blast.ncbi.nlm.nih.gov/Blast.cgi; Altschul et al. 1997) for preliminary identification (Table 1).
Nucleotide sequence accession numbers
Sequence data were deposited in the GenBank under accession numbers GQ451825—GQ451827 (Table 1).
Bacterial growth curves
Before the experiments, growth curves of the bacterial strains were established to characterize the different growth phases. Bacteria (except for strain MHWTa3) were inoculated into a fresh IBMG medium, and 1.5 ml samples were collected every 24 h for several days and fixed with formaldehyde (2% final concentration). Bacterial growth rates (μ) were calculated for the exponential phase according to the equation: μ = (ln N2 − ln N1)/(t2 − t1), where N2 and N1 are the number of cells at two different times. Generation times (g) were calculated as g = ln 2/μ.
For the experiments, three sets of muffled (450°C; 2 h) quartz tubes (n = 3) were filled with 100 ml of bacterial culture growing in IBMG and in the middle of the exponential phase. The first set of tubes was wrapped with a double layer of aluminum foil and served as dark control (DARK). The second set was wrapped with two layers of URUV foil (Digefra, Germany) that had 50% transmittance at 380 nm and excludes most of the UVR (PAR treatment), whereas the third set of tubes was exposed without further manipulation (PAR + UVR treatment). Simulated solar UVR was provided by four aged (100 h) fluorescent lamps (UVA-340, Q-Panel Co., Cleveland, OH, USA) with a maximum emission at 340 nm. The integrated irradiance between 280 and 320 nm (i.e., UV-B) was 1.4 W m−2 corresponding to a final dose of 20.2 kJ m−2, which is equivalent to a typical daily integrated value for summer at mid latitudes. PAR was provided by two white fluorescent tubes (cool white L36/W20, Osram) emitting 80 μmol quanta m−2 s−1. This PAR intensity is low compared to the natural solar spectrum and we have previously not observed negative effects on heterotrophic organisms, but it is efficient in promoting photorepair. A spectrum of the combination of lamps is found in Sommaruga et al. (1996).
Exposure took place in a walk-in room at 15°C for 4 h. During exposure, quartz tubes were kept horizontal at 25 cm distance from the lamps in a water bath to maintain constant temperature. Before (T0) and immediately after exposure (T4), samples were removed to estimate bacterial abundance, bacterial carbon production, and respiration rates. Bacterial abundance was checked again at the end of the respiration incubations (Tend) to control for potential changes. The incubations for respiration ranged between 8 and 14 h depending on the isolate (see bacterial respiration).
Samples for bacterial abundance (n = 3) were filtered onto black polycarbonate filters (Millipore GBTP, 0.22 μm pore size) and stained with DAPI (4′,6′-diamidino-2-phenylindole; Molecular Probes, Eugene, OR, USA) according to the method described by Porter and Feig (1980). At least 15 monochromatic pictures were taken using a charge coupled device (CCD) camera installed on an epifluorescence microscope (Zeiss Z1 Imager) equipped with a filter set for DAPI (Zeiss Nr. 1) at an overall magnification of 1,000×. More than 600 DAPI-positive cells were counted semi-automatically using the image analysis software Scoreedo (http://scoreedo.sengaro.net).
Bacterial carbon production (BCP)
Leucine incorporation rates were measured using [4,5-3H]-l-leucine (Amersham, specific activity = 17.7 GBq mmol−1) for strain MHWTa3 and [U-14C]-l-leucine (Amersham, specific activity = 11.3 GBq mmol−1) for the other strains at the final concentration of 20 nmol l−1 (Kirchman et al. 1985). One formaldehyde-fixed control and triplicate samples (5 ml) were incubated for 1 h at 15°C in the dark. Incubations were stopped by adding formaldehyde (2% final concentration). Then, samples were filtered onto 0.22-μm pore size polycarbonate filters (Millipore GTTP). The filters were rinsed twice with 5 ml of cold trichloroacetic acid (5%) for 5 min before being dissolved by adding 6 ml of scintillation cocktail (Ready-Safe, Beckman Coulter). Radioactivity was measured after 15 h in a scintillation counter (Beckman LS 6000IC). The conversion of bulk leucine incorporation rates (mol l−1 h−1) into bacterial carbon production (μg C l−1 h−1) was done using a conversion factor of 1.44 × Leuinc (Leuinc = leucine incorporation in mol) as recommended by Buesing and Marxsen (2005).
Bacterial respiration and bacterial growth efficiency
Bacterial respiration in the control and treatments was estimated from rates of oxygen consumption before and after exposure. Triplicate respiration glass microchambers (4 ml; Unisense, Denmark) were filled with 4 ml of culture and incubated in the dark. Oxygen concentration was measured immediately after filling the respiration chambers and at regular times using an oxygen microsensor OX-MR (Unisense, Denmark). This microsensor is designed with an exterior guard cathode (Revsbech 1989), which results in extremely low oxygen consumption by the electrode itself (1.5–15 × 10−8 mg O2 h−1, http://www.unisense.com). The microsensor and the gas tight microchambers allow highly precise repeated measurements to be done in every chamber without affecting the oxygen concentration. The microsensor has a response time shorter than 1 s and a precision of 0.05%, which is equivalent to the Winkler technique (Briand et al. 2004). All the measurements were done under temperature-controlled conditions, and temperature was kept constant (±0.1°C) during the whole incubation. Previous to the experiments, the oxygen consumption of the different bacterial strains was monitored during 16 h to define an appropriate incubation period, i.e., to detect a significant decrease in oxygen concentration. Accordingly, the following incubation times were chosen: 8 h (GKS12b, SOS1, and RC1), 11 h (MHWTa3), and 14 h (GKS10). The different times used, however, do not affect the comparisons because oxygen decrease was linear for all strains. Oxygen consumption was computed from the slope of oxygen concentration versus time and was converted into μg carbon respired per cell (DAPI abundance) assuming a respiratory quotient of 1 (del Giorgio and Cole 1998) and using the mean cell number of the beginning and the end of the respiration measurement. Bacterial growth efficiency (BGE) was computed as BGE (%) = Bacterial carbon production/(Bacterial carbon production + Bacterial respiration) × 100.
Effect of PAR + UVR on respiration of a natural bacterial community
On October 30 2007, a water sample was collected from Schwarzsee ob Sölden at 1 m depth with a Schindler-Patalas sampler (3 l). In the laboratory, the sample was filtered through a 0.8-μm polycarbonate membrane (ATTP, Millipore) to exclude organisms larger than bacteria and then was exposed as described above to PAR + UVR for 4 h or kept in the dark. Incubation and respiration measurements were done at 14°C.
One-way analysis of variance (ANOVA) was done on the dataset to test for significant differences between the control (DARK) and the treatments. To test for significant changes in bacterial abundance during exposure and respiration measurements (i.e., T0—T4 and T4—Tend) and in the different treatments, a one-way repeated measures ANOVA was used. The post hoc multiple comparisons of all ANOVAs were made pairwise by the Holm-Sidak method with an overall significance level of 0.05. Significant differences in the experiment with the natural bacterial assemblage were tested with a Student t-test. Statistical tests were carried out using SigmaStat (Systat, Software Inc., San Jose, CA).
Growth conditions and bacterial generation time
Changes in bacterial abundance during and after exposure
Bacterial respiration rate
Bacterial carbon production
The highest cell-specific bacterial carbon production in the DARK control corresponded to the RC1 strain (4.83 × 10−9 μg C cell−1 h−1), followed by GKS10 (3.31 × 10−9 μg C cell−1 h−1), GKS12b (2.21 × 10−9 μg C cell−1 h−1), SOS1 (1.03 × 10−10 μg C cell−1 h−1), and MHWTa3 (9.12 × 10−13 μg C cell−1 h−1). After exposure to PAR, no significant changes in bacterial carbon production were observed in all strains (Fig. 4). However, after exposure to PAR + UVR, bacterial carbon production significantly decreased in three out of five strains (Holm-Sidak, P < 0.05) showing a mean reduction of 97.8 ± 1.6% (GKS12b), 87.2 ± 0.9% (RC1), and 91.8 ± 3.0% (MHWTa3) when compared to the DARK control (Fig. 4). The decrease in bacterial carbon production of GKS10 (mean reduction of 36.0%) and SOS1 (mean reduction of 30.3%) after exposure to PAR + UVR was not significantly different from the DARK control (Fig. 4).
Bacterial growth efficiency
The highest BGE in the DARK was found in RC1 (42.3 ± 8.8%) followed by GKS10 (26.8 ± 7.0%) and SOS1 (0.6% ± 0.1), while the lowest value was detected in MHWTa3 (0.2% ± 0.08). Exposure to PAR did not have a significant effect on bacterial growth efficiency, except for strain GKS10 where it slightly increased (Fig. 4), whereas the effect of UVR was strain-specific. Thus, significantly lower bacterial growth efficiency values were found for RC1 (12.4 ± 1.0%) and for MHWTa3 (20.7 ± 11.5%) after exposure to PAR + UVR when compared to the DARK control (Fig. 4). The BGE in GKS10 decreased to 73.6 ± 4.8% in the presence of UVR, but the change was not significantly different when compared to the DARK (Fig. 4). By contrast, a significantly higher BGE value was found in SOS1 (Fig. 4).
Effect of PAR + UVR on respiration of a natural bacterial community
Our results showed that bacteria isolated from different freshwater habitats such as alpine lakes and rain, but grown under the same conditions, significantly differ in their growth efficiency even in the absence of UVR. Different growth efficiencies can result from the fact that even during unconstrained growth, bacteria use different amounts of energy for maintenance of metabolic processes instead of allocating it into new biomass (Russell and Cook 1995). Furthermore, variations in bacterial growth efficiency are often found when growth is limited by substrate availability (del Giorgio and Cole 1998). However, the latter source of variation can be neglected for the bacterial isolates we tested because they were in the exponential phase of growth. Whereas information on how efficiently aquatic bacteria convert DOM into bacterial biomass is essential to understand distribution patterns within bacterial communities, our experiment was not designed to resemble bacterial growth under natural conditions, where a complex mixture of different organic substrates is available. In fact, the growth efficiency values we estimated might be very different when bacteria grow in a more complex and organic-rich medium or in their original water (del Giorgio and Cole 1998). Our aim, however, was to be able to compare the effect of UVR on bacterial growth efficiency under the same conditions for all strains. Thus, whereas we cannot exclude probable physiological changes caused by the medium used, all isolates were able to reach exponential growth though at different rates (Fig. 1).
In general, exposure to UVR had an inhibitory effect on carbon production in all bacterial strains, although only in three strains a significant decrease was observed (Fig. 4a). This negative effect was also observed when changes in bacterial numbers were accounted for during the experiment (Figs. 2 and 4). Solar UVR and in particular the high energetic UV-B radiation (280–315 nm) is known to cause harmful effects in aquatic bacteria (Herndl and Obernosterer 2002; Buma et al. 2003), such as decrease in viability (Joux et al. 1999; Davidson and van der Heijden 2000; Agogué et al. 2005) or inhibition of secondary production (Herndl et al. 1993; Sommaruga et al. 1997; Hernandez et al. 2007). However, the sensitivity to UVR and the degree of damage are highly strain-specific (Arrieta et al. 2000; Zenoff et al. 2006b) and are affected among others factors by the existence of UVR protection mechanisms (Buma et al. 2003), previous exposure to increased levels of UVR (Gustavson et al. 2000), and DNA repair efficiency (Matallana-Surget et al. 2009).
Among the isolates tested in our study, the Gram-negative strain SOS1 (Acinetobacter lwoffii) had the highest rate of cell-specific bacterial production (Fig. 4a) and though there was a reduction (non significant) after exposure to UVR, this bacterium seems to be relatively tolerant against the stress imposed. In fact, strain SOS1 together with strain MHWTa3 were the only ones where a significant increase in bacterial abundance was observed during exposure to UVR, though afterward, numbers remained unchanged (Fig. 2). Strain SOS1 belongs to the Gammaproteobacteria and was isolated from the high-altitude lake Schwarzsee ob Sölden where this group comprises a very small fraction of the total bacterial community. Members of this group seem to be well adapted to the high UVR intensities present in this type of environment. In a study by Zenoff et al. (2006a), the unpigmented strain Acinetobacter johnsonii A6, isolated from an oligotrophic lake in the Antarctic, was similarly resistant to UVR as other Gram-positive pigmented bacteria tested in the same study. Members of the Acinetobacter group are unique regarding their high resistance to desiccation, H2O2 exposure, and even gamma radiation (La Duc et al. 2003). These findings indicate that despite weaker cell wall characteristics than Gram-positive bacteria and lack of pigmentation, representatives of this group are highly tolerant to UVR.
Similar to SOS1, GKS10 (Sphingomonas sp. B14) showed no significant reduction in bacterial carbon production after exposure to UVR (Fig. 4a), suggesting a high tolerance. Members of the genus Sphingomonas seem to be highly resistant to UV-B radiation due to their low accumulation of cyclobutane pyrimidine dimers (Joux et al. 1999). Additionally, many strains of Sphingomonas have pigments (also strain GKS10, Table 1) that can probably minimize the negative effects of UVR (Buma et al. 2003). By contrast, strains GKS12b (Acidovorax sp.), RC1 (Pseudomonas sp.), and MHWTa3 (Actinobacterium MHWTa3 showed a high UV sensitivity (Fig. 4a). Whereas information on UV sensitivity of members of the genus Acidovorax or Actinobacterium is not available, that on Pseudomonas suggests that members of this genus can be very sensitive to UVR (Fernández and Pizarro 1996; Zenoff et al. 2006b) and may lack DNA repair mechanisms (Simonson et al. 1990; Kidambi et al. 1996). Interestingly, despite their presumable high sensitivity to UVR, members of the genus Pseudomonas are known to be transported through the atmosphere (Amato et al. 2007), where a general stress tolerance is probably necessary.
Regarding bacterial respiration, no general trend was observed after exposure to UVR. Although bacterial respiration decreased in three strains, only SOS1 showed a significant decrease (Fig. 4b). The undetectable bacterial respiration values in strain GKS12b suggest also a severe inhibition (Fig. 5). By contrast, the increase in bacterial respiration found in RC1 (Fig. 4b and 5) could be an indication of a high sensitivity to UVR because metabolic reactions and associated biochemical oxygen demand tend to increase under physiological stress (Aertsen and Michiels 2004; Hecker et al. 2007).
Antagonistic results of UVR effects on respiratory activity have been found for several bacterial freshwater communities. For example, Rae and Vincent (1998) found a significant UV inhibition of actively respiring bacteria, while Ferreyra et al. (1997) detected significantly higher electron transport system activities and consequently higher bacterial respiration in a natural plankton community after exposure to UV-B radiation. Probable reasons for those contrasting results can be differences in bacterial community composition (Reinthaler et al. 2005), as well as changes in bacterial community structure during respiration measurements (Gattuso et al. 2002). Our own results with the natural bacterial community of Schwarzsee ob Sölden indicate that UVR resulted in higher oxygen consumption rates (Fig. 6). These results are interesting because they illustrate the contrasting response of the whole bacterial community (i.e., ‘black box’ approach) and strain SOS1 isolated from the same lake. Though we do not know what the representation of strain SOS1 was in the natural bacterial community of Schwarzsee ob Sölden at the time of the experiment, these results suggest that it may be difficult to interpret bulk respiration rates in natural bacterial communities exposed to solar UVR.
The tested isolates showed contrasting changes in their bacterial growth efficiency after exposure to UVR (Fig. 4c). Different bacterial isolates are known to vary in their sensitivity to UVR (Fernández and Pizarro 1996; Arrieta et al. 2000), but hardly any information is available on changes of strain-specific bacterial growth efficiency after UV exposure. Although the strong inhibition of bacterial growth efficiency by UVR was not totally unexpected, we did not anticipate to observe a negative effect for widespread bacterial taxa such as Acidovorax and Pseudomonas (Fig. 4C). Members of those groups have been found in various freshwater systems and are present even in extreme habitats with high UVR conditions (Amato et al. 2007; Hervàs et al. 2009). Generally, bacterial isolates display large interspecific differences in their recovery efficiencies after UV exposure, as shown for marine bacterioplankton (Kaiser and Herndl 1997) and for marine bacterial isolates (Joux et al. 1999; Arrieta et al. 2000). Strains of Acinetobacter johnsonii were found to endure and even to recover very rapidly from UV damage, despite high accumulation of cyclobutane pyrimidine dimers (Zenoff et al. 2006b). By contrast, strains of Pseudomonas spp. do not recover (Zenoff et al. 2006b). In our study, SOS1 (Acinetobacter lwoffii, Fig. 4C) was the only strain showing a high tolerance and even a significant increase in bacterial growth efficiency after UV exposure. This strain probably has effective repair mechanisms that allows for maintaining cell production and thus to increase bacterial growth efficiency after UV exposure. The second strain showing signs of UV tolerance and a relatively low decrease in bacterial growth efficiency after UV exposure was GKS10 (Sphingomonas sp. B14, Fig. 4c).
Overall, strain-specific effects on bacterial growth efficiency were mainly driven by the changes in bacterial production. These results agree with those of other studies (Toolan 2001; Reinthaler and Herndl 2005) that showed growth efficiencies of natural bacterial assemblages mainly reflect changes in bacterial production rather than in respiration. Nevertheless, as shown in our study, the effect of UVR on bacterial respiration was strain-specific and rates decreased or increased after exposure. Though in the experiment with the natural bacterial community of Schwarzsee ob Sölden, we did not measure bacterial production concomitantly; previous results from a transparent alpine lake such as this showed that this process is strongly inhibited by UVR (Sommaruga et al. 1997). Thus, the most probable outcome of the effect of UVR on this natural bacterial community was a reduction in bacterial growth efficiency.
In summary, our findings indicate that changes in metabolic rates caused by UVR were highly strain-specific and that variations in bacterial growth efficiency mainly reflected the response in production of new bacterial biomass to this environmental stressor. Our results underline the role UVR has in potentially altering the efficiency by which the dissolved organic matter pool is transformed into bacterial biomass in aquatic ecosystems. Furthermore, the alterations caused by UVR may have consequences for the efficiency of carbon cycling, especially considering that climate change will affect the UV transparency of freshwaters (Adrian et al. 2009).
We thank J. Hofer for helping with the isolation and cultivation of bacterial strains, S. Morales-Gómez for helping to determine bacterial numbers, M. Hahn for providing isolate MHWTa3, and two anonymous reviewers for their comments. This work was supported by the Austrian Science Fund (FWF) through a research project (P19245-BO3) to R. Sommaruga.
This article is distributed under the terms of the Creative Commons Attribution Noncommercial License which permits any noncommercial use, distribution, and reproduction in any medium, provided the original author(s) and source are credited.
- Briand E, Pringault O, Jacquet S, Torreton JP (2004) The use of oxygen microprobes to measure bacterial respiration for determining bacterioplankton growth efficiency. Limnol Oceanogr Meth 2:406–416Google Scholar
- Buesing N, Marxsen J (2005) Theoretical and empirical conversion factors for determining bacterial production in freshwater sediments via leucine incorporation. Limnol Oceanogr Meth 3:101–107Google Scholar
- Buma AGJ, Boelen P, Jeffrey WH (2003) UVR-induced DNA damage in aquatic organsims. In: Helbling EW, Zagarese HE (eds) UV effects in aquatic organisms and ecosystems. Royal Society of Chemistry, Cambridge, UK, pp 293–327Google Scholar
- Gottschalk G (1986) Bacterial metabolism. Springer-Verlag, New York 359 pGoogle Scholar
- Herndl GJ, Obernosterer I (2002) UV radiation and pelagic bacteria. In: Hessen DO (ed) UV Radiation and Arctic Ecosystems. Ecological Studies, vol 153. Springer-Verlag, Berlin, pp 245–259Google Scholar
- Jeffrey WH, Kase JP, Willhelm SW (2000) UV radiation effects on heterotrophic bacterioplankton and viruses in marine environment. In: de Mora S, Demers S, Vernet M (eds) The effects of UV radiation in the marine environment. Cambridge University Press, Cambridge, pp 206–236Google Scholar