Editor: Patricia Sobecky
Abundance and diversity of aerobic anoxygenic phototrophic bacteria in saline lakes on the Tibetan plateau
Version of Record online: 5 NOV 2008
© 2008 Federation of European Microbiological Societies. Published by Blackwell Publishing Ltd. All rights reserved
FEMS Microbiology Ecology
Volume 67, Issue 2, pages 268–278, February 2009
How to Cite
Jiang, H., Dong, H., Yu, B., Lv, G., Deng, S., Wu, Y., Dai, M. and Jiao, N. (2009), Abundance and diversity of aerobic anoxygenic phototrophic bacteria in saline lakes on the Tibetan plateau. FEMS Microbiology Ecology, 67: 268–278. doi: 10.1111/j.1574-6941.2008.00616.x
- Issue online: 22 DEC 2008
- Version of Record online: 5 NOV 2008
- Received 15 April 2008; revised 30 August 2008; accepted 17 September 2008.First published online 5 November 2008.
- AAP bacteria;
- Qinghai Lake
- Top of page
- Materials and methods
Aerobic anoxygenic phototrophic (AAP) bacteria are heterotrophic prokaryotes that are capable of utilizing light as an energy source but are not capable of producing molecular oxygen. Recently, multiple studies have found that AAP bacteria are widely distributed in oceans and estuaries and may play an important role in carbon cycling. However, AAP bacteria in inland lake ecosystems have not been investigated in depth. In this study, the abundance and diversity of the pufL-M genes, encoding photosynthetic reaction centers of AAP bacteria, were determined in the oxic water column and anoxic sediments of saline lakes (Qinghai, Erhai, and Gahai Lakes) on the Tibetan Plateau, China. Our results indicated that AAP bacteria were abundant in inland lakes, with the proportion of AAP bacteria (in total bacteria) comparable to those in the oceans, but with a lower diversity. Salinity and pH were found to be potential factors controlling the AAP bacterial diversity and community composition. Our data have implications for a better understanding of the potential role of AAP bacteria in carbon cycling in inland lake ecosystems.
- Top of page
- Materials and methods
Aerobic anoxygenic phototrophic (AAP) bacteria are a group of heterotrophic prokaryotes capable of utilizing light as an energy source but are not capable of producing molecular oxygen (Yurkov & Beatty, 1998a, b; Beatty, 2002). Studies have revealed that AAP bacteria are widely distributed in various habitats, including marine environments, acidic mine drainage, and hot springs (Yurkov & Beatty, 1998b), rivers and estuaries (Waidner & Kirchman, 2005, 2007, 2008), as well as inland lakes (Yurkova et al., 2002; Karr et al., 2003; Page et al., 2004; Gich & Overmann, 2006; Masin et al., 2008). AAP bacteria can account for a large portion (several percent to more than half) of the total bacterial community in various aquatic ecosystems (Kolber et al., 2001; Du et al., 2006; Jiao et al., 2007; Waidner & Kirchman, 2007; Masin et al., 2008), that is, several to about 10% of the total bacterial community in the ocean (Kolber et al., 2001), up to 34% in estuaries (Waidner & Kirchman, 2007), and more than half in freshwater mountain lakes (Masin et al., 2008). AAP bacterial biomass showed significant spatial and temporal variations in the global oceans (Jiao et al., 2007; Zhang & Jiao, 2007) and freshwater mountain lakes (Masin et al., 2008).
Phylogenetic analysis based on the pufL-M genes suggests that most, if not all, AAP bacteria belong to the alpha-, beta-, and gamma-subclasses of Proteobacteria (Yutin & Beja, 2005), and that AAP bacterial community composition varies with respect to different ecosystems. Alphaproteobacterial and gammaproteobacterial AAP bacteria are abundant in saline water bodies (such as oceans, lakes and estuaries), whereas betaproteobacterial AAP bacteria are predominant in freshwater bodies (Yurkova et al., 2002; Allgaier et al., 2003; Karr et al., 2003; Koblížek et al., 2003; Oz et al., 2005; Waidner & Kirchman, 2005, 2007, 2008; Cho et al., 2007; Jiao et al., 2007). Light, dissolved organic carbon (DOC), salinity, and association with particles may control the AAP bacterial abundance and distribution in estuaries and oceans (Jiao et al., 2007; Zhang & Jiao, 2007; Waidner & Kirchman, 2008).
Despite the fact that saline lakes account for almost half of the total volume of all terrestrial aquatic ecosystems (William, 1996), little is known about the diversity and abundance of AAP bacteria in such ecosystems. Are AAP bacteria in saline lakes more abundant and/or diverse than the oceans? How does the AAP bacteria community respond to salinity gradient? In this study, we strive to answer these questions by investigating the abundance and diversity of AAP bacteria in three saline lakes on the Tibetan Plateau in NW China: Qinghai Lake (36°32′–37°15′N, 99°36′–100°47′E) and two of its daughter lakes (Gahai Lake and Erhai Lake). Multiple methods were used including aqueous geochemistry, time-series observation-based infrared epifluorescence microscopic (TIREM) counting of AAP bacteria, quantitative PCR (qPCR) determination of functional genes (pufL-M), and functional gene-based diversity analysis.
Qinghai Lake is the largest (4300 km2) saline (12.5 practical salinity unit, PSU) and alkaline (pH 9.3) lake on the Tibetan Plateau (Dong et al., 2006), and it represents a relatively pristine environment, where perturbations from human activities have been small. Because of the continuous drying, Gahai Lake (c. 35 km2) and Erhai Lake (c. 5 km2) have been isolated from Qinghai Lake since the Holocene. Because of different water dynamics, these lakes have developed into a salinity gradient (Gahai Lake>Qinghai>Erhai Lake) but their water chemistry is similar (CAS, 1979). Thus, studies of AAP bacteria abundance and diversity in these lakes can fill the aforementioned knowledge gap.
Materials and methods
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- Materials and methods
Description of the study site
Qinghai Lake is a perennial lake located in a structural intermontane depression at the northeastern corner of the Tibetan Plateau (Fig. 1). The average water depth is 19.2 m, and the maximum is 28.7 m. The altitude of the lake is 3196 m above sea level (m a.s.l.), and the surrounding mountains rise to above 5200 m a.s.l. (Dong et al., 2006). The water column of Qinghai Lake is fairly dynamic, with limited seasonal stratification (CAS, 1979; Dong et al., 2006). The main (80%) water supplies to Qinghai Lake are inflowing rivers, which are mostly distributed on the southwest, northwest, and north of the lake. The remaining 20% of the water supplies are springs at the bottom of Qinghai Lake and rainfalls (CAS, 1979). The evaporation of the lake (c. 1400 mm year−1) is in excess of the mean annual water replenishment (c. 400 mm year−1), resulting in the development of a saline lake with a salinity of 12.5 PSU (Shen et al., 2005; Dong et al., 2006) and formation of isolated daughter lakes on the eastern edge of the lake. Gahai Lake and Erhai Lake are two representative daughter lakes. The area of Gahai and Erhai is c. 47.2 and c. 5 km2, and the maximum water depth is 9 and 2.0 m, respectively.
Sample collection and processing
In July 2007, three sites (36.735°N/100.355°N, 36.992°N/100.611°E, and 36.546°N/100.722°E from Qinghai Lake, Gahai Lake, and Erhai Lake, respectively) were selected for in situ measurement of lake water chemistry and sampling. The Qinghai Lake site was also selected for sediment core collection (Fig. 1). In situ measurements of water geochemistry were performed using a multiple parameter probe set Horiba (Japan). Water depth was 23, 0.5, and 0.5 m at the sampling sites of Qinghai Lake, Erhai Lake, and Gahai Lake, respectively. A 56-cm-long sediment core (QL, abbreviation of Qinghai Lake) was retrieved by a gravity-coring device and immediately frozen in dry ice. At the site of Qinghai Lake, depth profiles of lake water geochemistry were measured every 2 m from a large boat. For Gahai Lake and Erhai Lake, only the surface water was selected for in situ water geochemical analyses and sample collection. The geochemical parameters included pH, conductivity, turbidity, dissolved oxygen (DO), temperature, salinity, total dissolved solids, density, oxidation–reduction potential, and concentrations of nitrate, chloride, and ammonia (H. Jiang et al., unpublished data). Based on these measurements, four depths (0, 5, 12, and 23 m) of the Qinghai Lake water column were selected for molecular microbiology by pumping lake water using a submersible pump. At the same depths, water samples were collected for analysis of dissolved inorganic and organic carbon (DIC and DOC). DIC samples were collected in 20-mL Teflon cap glass bottles and preserved with 200 mL saturated HgCl2 to stop any biological activity. DOC samples were filtered through <0.45-μm filters and collected into 20-mL Teflon cap glass bottles. DOC samples were immediately frozen in dry ice. Microbial samples were collected by on-line filtering of c. 500 mL of lake water through 0.2-μm filters (Millipore), and the filters were immediately frozen in dry ice. In November 2007, triplicate water samples were collected from the edge of Qinghai Lake (36°34′N, 100°42′E) (Fig. 1).
All the samples for molecular work were stored in liquid nitrogen from the date of collection until analysis. In <1 week, the samples were taken to China University of Geosciences in Beijing, where they were stored in a −80 °C freezer. The sediment core was dissected according to our established procedure (Jiang et al., 2008). Sediment subsamples were collected every 10–20 cm with a total of five for the QL core (56 cm in length).
DOC and DIC samples were analyzed at the State Key Laboratory of Marine Environmental Science at Xiamen University, China. DOC was measured from acidified samples using a high-temperature catalytic oxidation analyzer (Shimadzu TOC-V) (Sharp et al., 1995, 2002). DIC concentration was determined using a Li-Cor® nondispersive IR detector (Li-6252) after the sample was acidified (Wang & Cai, 2004). Total nitrogen (TN) and Total phosphorus (TP) were measured according to standard methods (Jin & Tu, 1990). Sediment pore water samples were collected and analyzed for pH, anions, and cations in the laboratory according to our previously established protocols (Jiang et al., 2008). Major anions and cations were combined to calculate salinity (PSU).
AAP bacterial cell counts
Water samples were fixed for 15 min with paraformaldehyde (2%, final concentration) and then stained with 4′6-diamidino-2-phenylindole (5 μg mL−1, final concentration) for 30 min in the dark. Cells were filtered onto 0.2 μm pore-size black polycarbonate membranes (Whatman) for counting. The abundance of AAP bacteria was determined by the TIREM protocol as described previously (Jiao et al., 2006, 2007).
DNA isolation, PCR amplification, and phylogenetic analysis
Six water samples (four from Qinghai Lake, at 0, 500, 1200, and 2300 cm depth, respectively, and one each from Gahai Lake and Erhai Lake, respectively) and two sediment subsamples (0 and 52 cm from the QL core) were subjected to community DNA extraction using the FastDNA® SPIN Kit for soil (Qbiogene Inc., Irvine, CA) according to the protocol of the manufacturer. The partial pufL-M genes of the extracted DNA samples were amplified using the primer set of pufL forward (5′-CTK TTC GAC TTC TGG GTS GG-3′) and pufM reverse (5′-CCA TSG TCC AGC GCC AGA A-3′) (Nagashima et al., 1997; Beja et al., 2002) using the FailSafe™ PCR System (Epicentre Inc.). PCR conditions were as follows: 94 °C for 5 min; 40 cycles of denaturing (30 s at 94 °C), annealing (30 s at 55 °C), and extension (2 min at 72 °C); and a final extension at 72 °C for 7 min. The PCR products were purified using the GeneClean® Turbo kit (Qbiogene Inc.) according to the manufacturer's protocol (Jiang et al., 2006). Eight pufL-M gene clone libraries (Erhai Lake-W; Gahai Lake-W; QL-0-W at 0 cm of the Qinghai Lake water column; QL-500-W, 500 cm; QL-1200-W, 1200 cm; and QL-2300-W, 2300 cm; QL-0-S, at 0 cm of the sediment core; QL-52-S, 52 cm) were constructed according to previous procedures (Jiang et al., 2006). Approximately 30 randomly selected colonies per sample were analyzed for insert pufL-M gene sequences. Plasmid DNA of randomly selected clones was extracted using the QuickClean 5M Miniprep Kit (GenScript Corporation, Piscataway, NJ). The pufL-M gene fragments of selected clones were sequenced using pufM reverse primer with the BigDye Terminator version 3.1 chemistry (Applied Biosystems, Foster City, CA). The pufL-M gene sequences were determined using an ABI 3730 automated sequencer. Nucleotide sequences were assembled and edited using sequencer v.4.1 (GeneCodes, Ann Arbor, MI). Clone sequences showing 97% similarity or higher were considered to be the same group (Jiao et al., 2007). One sequence from each group was then selected as a representative for phylogenetic analysis. Neighbor-joining phylogenies were constructed from dissimilar distance and pairwise comparisons with the Jukes–Cantor distance model using the mega (molecular evolutionary genetics analysis) program, version 4.1. Shannon–Weaver diversity indices of all clone libraries were then calculated at the group level using the past program (http://folk.uio.no/ohammer/past/). Coverage (C) was calculated as follows: C=1−(n1/N), where n1 is the number of phylotypes that occurred only once in the clone library and N is the total number of clones analyzed. The sequences determined in this study were deposited in the GenBank database under accession numbers EU371072–EU371104.
Copies of the pufL-M genes and bacterial/archaeal 16S rRNA gene in selected samples were determined by qPCR according to the protocols of Du et al. (2006) and our previous study (Jiang et al., 2007), respectively. Amplification conditions were 50 °C for 2 min, and then 95 °C for 15 min, followed by 45 cycles (15 s at 94 °C, 30 s for annealing at 53 °C, and 30 s at 72 °C) in a reaction volume of 25 μL, containing 12.5 μL of QuantiTect SYBR-Green Master Mix (QIAGEN, Valencia, CA) and 2.5 pmol of each primer. Purified plasmid DNA of Clone QL-0-WP18 (obtained in this study) was used as a standard, which, with serial dilutions, was used to yield the standard curve. In order to evaluate the ratio of AAPB to total bacteria in the samples, total bacterial 16S rRNA gene copies were also determined by qPCR with the use of the primer set of Bac331F (5′-TCC TAC GGG AGG CAG CAG T-3′)/Bac797R (5′-GGA CTA CCA GGG TCT AAT CCT GTT-3′) (Nadkarni et al., 2002) according to the conditions outlined in our previous study (Jiang et al., 2007). All qPCR reactions were performed in duplicate. R2 values of the standard curves were 0.999 and 0.997 for the pufM and total bacterial 16S rRNA genes, respectively. All qPCRs were performed using a Rotor-Gene ™3000 real-time thermal cycler (Corbett Life Science, Sydney, Australia). Melting curve analysis was performed to determine the melting point of the amplification products and to assess reaction specificity. After the qPCR reaction was complete, the temperature was ramped from 72 to 95 °C, increasing by 0.1 °C each step, waiting for 45 s at the first step, and then 5 s for each subsequent step. The melting curve had only one peak, indicating that the SYBR green signals were not from primer–dimer artifacts and/or nonspecific DNA contamination.
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- Materials and methods
Lake water chemistry
Both pH and salinity increased from Erhai Lake to Qinghai Lake to Gahai Lake (Table 1). The major cations and anions were Na+ and Cl− for all three lakes (data not shown). Qinghai Lake was fairly dynamic, without stratification in the water column (data not shown; H. Jiang et al., unpublished data). In Qinghai Lake, the DIC concentration was fairly constant throughout the water column, ranging from 20.9 to 22.4 mmol L−1. The DOC concentration was in the range of 9.7–14.2 C-mg L−1. DIC concentrations for Erhai and Gahai were lower than those in Qinghai Lake (Table 1), but DOC concentrations were much higher than those in Qinghai Lake. The pH and salinity value for the pore water of the sediment core at 52 cm depth was 9.50 and 8 PSU, respectively.
|Area (km2)||Maximum depth (m)||Sampling depth (m)||pH||Conductivity (ms m−1)||DO (mg L−1)||Turbidity (mg L−1)||Temperature (°C)||Salinity (PSU)||TN (mg L−1)||TP (mg L−1)||DOC (C mg L−1)||DIC (mmol L−1)|
|Erhai||5||2||0||9.83||9.175||7.57||27.9||19.4||9.8||2.3||0.165||31.0 ± 3.2||9.9 ± 0.1|
|Gahai||47.2||9.25||0||9.33||4.12||4.85||0||16.1||32||2.1–2.9||0.04–0.08||35.2 ± 9.4||21.7 ± 0.2|
|Qinghai water column||4340||28.7||0||9.46||2.01||5.4||0||15.5||14.3||0.9||0.012||10.0 ± 0.2||21.6 ± 0.1|
|6||9.50||2.01||5.61||0||14.9||14.3||0.9||0.01||9.7 ± 0.2||21.4 ± 0.2|
|12||9.50||2.01||6.4||0||13.2||14.3||1.0||0.01||9.9 ± 0.3||21.1 ± 0.3|
|23||9.39||2.03||7.03||0||11.4||14.3||1.0||0.02||9.4 ± 0.1||21.7 ± 0.1|
AAP bacteria abundance determined by TIREM and qPCR
The TIREM and qPCR data were consistent with each other (Table 2). Among the three studied lakes, Qinghai Lake had the highest AAP bacteria abundance, followed by Erhai Lake and Gahai Lake. The Qinghai Lake sample collected in November 2007 had the highest AAP bacteria abundance. The number of AAP bacteria pufL-M gene copies in the Qinghai Lake sediments was below the detection limit (<102 copies g−1 sediment).
|AAP bacteria (cell mL−1)||AAP bacteria*,† (%)||Total prokaryotes (bacteria+archaea)||AAP bacteria (cell mL−1)||AAP bacteria*,†,‡ (%)|
|Erhai Lake||1.13E+04 ( ± 1173)||1.57 ± 0.23||1.38E+06 ( ± 28 260)||Not available||Not available|
|Gahai Lake||9.60E+03 ( ± 589)||0.95 ± 0.09||1.36E+06 ( ± 11 600)||4.75E+03 ( ± 3360)||0.54|
|QL-0-W||4.60E+04 ( ± 2371)||5.23 ± 0.91||1.89E+05 ( ± 5480)||1.91E+04 ( ± 4356)||3.16|
|QL-500-W||4.34E+04 ( ± 2935)||4.24 ± 0.67||2.79E+05 ( ± 31 533)||1.20E+04 ( ± 707)||1.72|
|QL-1200-W||4.06E+04 ( ± 1877)||5.35 ± 0.43||5.11E+05 ( ± 46 000)||5.96E+04 ( ± 8577)||5.36|
|QL-2300-W||4.16E+04 ( ± 2199)||4.52 ± 0.59||5.47E+05 ( ± 68 880)||2.21E+04 ( ± 2402)||1.68|
|QL surface water§||Not determined||Not determined||Not determined||9.84E+04 ( ± 47 487)||8.98|
|QL-0-S1||Not detectable||Not detectable||1.88E+08 ( ± 3 990 000)¶||Not determined||Not determined|
|QL-52-S1||Not detectable||Not detectable||3.99E+08 ( ± 25 900 000)¶||Not determined||Not determined|
Diversity of AAP bacteria
A total of 210 AAP bacteria pufL-M gene clone sequences (102, 26, and 25 clones from the water samples of Qinghai Lake, Gahai Lake, and Erhai Lake, respectively; 57 clones from the Qinghai Lake sediments) were subjected to sequence similarity analysis (Table 3). These sequences belonged to Alpha- and Gammaproteobacteria (Fig. 2). The Alphaproteobacteria group could be classified into eight clusters: Loktanella-like, Roseobacter-like, Sphingomonas-like, Rubritepida-like, Porphyrobacter/Erythrobacter-like sequences, and three unknown subgroups (Fig. 3). The group affiliation analyses of these sequences showed distinct differences in their relative abundance among either the three lakes or different depths of the Qinghai Lake water column (Fig. 3). In Erhai Lake, the AAP bacteria community was composed of four groups: Gammaproteobacteria-like, Sphingomonas-like, Rubritepida-like, and the unknown group-3, among which the Gammaproteobacteria-like sequences were predominant. In contrast, AAP bacteria pufL-M gene clone sequences in Gahai Lake consisted of only one major group: Loktanella-like, which was absent in Erhai Lake (Fig. 3).
|Clone libraries||Total clones sequenced||Coverage (%)||No. of groups||SW*-diversity index||pH||Salinity (PSU)|
In Qinghai Lake, whose salinity (c. 12.5 PSU) and pH (9.4–9.5) were between Erhai Lake and Gahai Lake, the AAP bacteria community was mainly composed of the Loktanella-like group, with a few other groups in smaller proportions: Roseobacter-like, Porphyrobacter/Erythrobacter-like, Gammaproteobacteria-like, and the unknown group-1. Although the water column of Qinghai Lake was not stratified, the AAP bacteria community composition did not appear to be completely mixed (Fig. 3): at the depth of 0 cm (near the surface of the water column), the AAP bacteria community consisted of Loktanella-like, Roseobacter-like, Porphyrobacter/Erythrobacter-like, and unknown group-1 sequences. At the depth of 500 cm, the AAP bacteria community was composed of Loktanella-like, Roseobacter-like, and unknown group-1 sequences. The Loktanella-like sequences were the only phylogenetic group at the depth of 1200 cm. Three groups (Gammaproteobacteria-like, Loktanella-like, and Roseobacter-like) were predominant at the depth of 2300 cm.
The sequenced clones in each library covered 96–100% diversity (Table 3). The Shannon–Weaver indices for the Erhai Lake water/Qinghai Lake sediments, the Qinghai Lake water column, and the Gahai Lake water were c. 1.4, c. 0.9–1.1 (except for the depth of 1200 cm), and c. 0.5, respectively (Table 3). The diversity indices of the pufL-M gene clone libraries in the studied lake waters appeared to be in inverse correlation with salinity.
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- Materials and methods
AAP bacteria are able to supplement their aerobic respiration with photosynthesized ATP, thus conserving organic carbon (Kolber et al., 2000, 2001). Because of such a unique role in global carbon cycling, AAP bacteria have increasingly drawn researchers' attention since the last decade. However, little is known about the abundance and diversity of AAP bacteria in high-elevation saline lakes.
AAP bacteria abundance
The abundance of AAP bacteria varies considerably in aquatic environments (Kolber et al., 2001; Schwalbach & Fuhrman, 2005; Cottrell et al., 2006; Sieracki et al., 2006; Lami et al., 2007), with estuaries and mountain lakes having a high abundance (Schwalbach & Fuhrman, 2005; Waidner & Kirchman, 2007). The reasons for such a large variation are not clear, although environmental nutrient status (Kolber et al., 2001; Waidner & Kirchman, 2007; Masin et al., 2008), light intensity (Waidner & Kirchman, 2007), associations with sediment particle (Waidner & Kirchman, 2007), and chlorophyll a concentration (Jiao et al., 2007) have been hypothesized to be some variables responsible for this variation. In the three Tibetan lakes studied, the fractions of AAP bacteria (i.e. the percentage of AAP bacteria in total bacteria) were comparable to the levels detected in the Indian (3.79 ± 1.72%), the Atlantic (1.57 ± 0.68%), and the Pacific (1.08 ± 0.74%) oceans (Table 2), but much lower than those in freshwater lakes of an oligotrophic to a mesotrophic nature (7–80% depending on seasonality and nutrient levels) (Masin et al., 2008) and in estuaries (Waidner & Kirchman, 2007, 2008). The lakes with the higher DOC content (i.e. Erhai and Gahai) exhibited lower AAP bacteria abundance, consistent with results from a previous study (Masin et al., 2008).
AAP bacterial diversity
The overall diversity of AAP bacteria was low in the Tibetan lakes. The AAP bacterial diversity decreased as the salinity and pH increased (Fig. 3, Table 3). Among the three lakes studied, Gahai Lake with the highest salinity and pH exhibited the lowest AAP bacteria diversity, Erhai Lake with the lowest salinity and pH had the highest diversity, and Qinghai Lake with an intermediate salinity and pH showed an intermediate diversity. Of the limited environmental factors examined, salinity and pH appeared to be important in controlling AAP bacteria diversity. Interestingly, the sediment sample at the 52 cm depth of Qinhai Lake had a salinity similar to the Erhai water column (c. 8 PSU) and, correspondingly, the AAP bacteria diversity for the QL-52-S sample was similar to that for Erhai (Table 3 and Fig. 3), further demonstrating that salinity might be one of the important factors in controlling AAP bacteria diversity in these lakes. However, this salinity–diversity relationship did not appear to hold true across different ecosystems. For example, the salinity in all three lakes studied was lower than that of seawater, but the AAP bacteria diversity was qualitatively lower than that in oceans. This complication suggests that a number of other factors could drive AAPB diversity (such as light availability, N and P availability, and UV irradiance) (Jiao et al., 2007 and references therein). In addition, ecosystem size and evolution time may be important factors accounting for this complication, but they were not examined in this study.
Despite recent advances in studies of AAP bacteria in many different environments, the relationship between environmental controlling factors and AAP bacterial community composition is still poorly understood. It appears that in saline water bodies (such as oceanic and coastal waters, lakes, and the saline side of estuaries), AAP bacteria belonging to Alphaproteobacteria and Gammaproteobacteria are dominant (Yurkova et al., 2002; Allgaier et al., 2003; Koblížek et al., 2003; Oz et al., 2005; Waidner & Kirchman, 2005, 2007, 2008; Cho et al., 2007; Jiao et al., 2007). In freshwater lakes and the freshwater side of estuaries, Betaproteobacteria are predominant (Karr et al., 2003; Waidner & Kirchman, 2005, 2008). This distribution pattern of AAB bacteria is similar to that defined by the 16S rRNA gene, i.e. with increased salinity, the relative abundance of Alphaproteobacteria and Gammaproteobacteria increases, but that of Betaproteobacteria decreases (Wu et al., 2006; Dong & Yu, 2007; references therein).
Consistent with this distribution pattern, our phylogenetic analysis revealed that the AAP bacterial community structure in the Tibetan saline lakes was dominated by Alpha- and Gammaproteobacteria, broadly similar to the AAP bacterial community structure in oceans. Indeed, Yurkova et al. (2002) observed a close phylogenetic relation of some strains purified from a meromictic lake (Mahoney Lake in British Columbia) to species obtained from marine environments. This observation implies that the similar environmental conditions of saline lakes (including Mahoney Lake) and the oceans (i.e. pH, salinity, and water chemistry) may have been responsible for the similar AAP bacterial community structure. Interestingly, Jiang et al. (2008) observed archaeal biogeography where similar environmental conditions between Qinghai Lake and the world oceans resulted in a similar archaeal community structure. However, a closer examination at a finer phylogenetic resolution reveals differences in the AAP bacterial community structure between the oceans and the Tibetan lakes studied. For example, Roseobacter- and Erythrobacter-related AAP bacterial clone sequences of Alphaproteobacteria were ubiquitous in the major ocean regimes (Jiao et al., 2007), but Loktanella-like sequences of Alphaproteobacteria were predominant in the Tibetan lakes (this study). Considering that AAP bacteria require light for energy, it is not surprising to observe such a difference, because of drastically different elevations and thus light intensities between Qinghai Lake and the oceans.
It is remarkable to note that the AAP bacterial community structure of Erhai Lake was completely different from that of either Qinghai or Gahai Lake. This difference could not be solely ascribed to salinity, because the salinity contrast between Erhai Lake and Qinghai Lake/Gahai Lake was not as great as between freshwater and seawater in the Delaware estuary (Waidner & Kirchman, 2008). The AAP bacterial community structure from Erhai Lake (with the lowest salinity, 9.8 PSU) was not dominated by freshwater Betaproteobacteria-like, but by saline water Gammaproteobacteria-like AAP bacterial sequences. An important difference between Erhai Lake and Qinghai/Gahai Lake was turbidity (Table 1). Whereas Erhai Lake was turbid, Qinghai and Gahai Lakes were clear. Thus, it was reasonable to speculate that the AAP bacteria detected in Erhai may largely be associated with sediment particles, whereas AAP bacteria in Qinghai/Gahai Lakes were mostly free-living. Previous studies observed that particle-attached and free-living bacterial community composition is fundamentally different (DeLong et al., 1993; Crump et al., 1999; Phillips et al., 1999; Schweitzer et al., 2001; Acinas et al., 2005). It has been shown that most AAP bacteria are associated with particles, and this attachment apparently increases their competitiveness in estuary environments (Yutin et al., 2007; Waidner & Kirchman, 2008).
Although the Qinghai Lake water column was vertically mixed with only slight stratification of geochemical variables (Table 1) and there was no systematic decline in the AAP bacteria abundance with increased depth, the AAP bacteria community composition did vary with depth. This variation may be partly caused by decreased light intensity with depth. It is well established that light intensity affects pigment formation necessary for photosynthesis (Aagaard & Sistrom, 1972; Drews & Golecki, 1995). Blue light inhibits photosynthetic pigment accumulation in Roseobacter denitrificans (Iba & Takamiya, 1989; Takamiya et al., 1992). The fact that the Roseobacter-like pufL-M sequences at the bottom were more abundant than the top of the water column in Qinghai Lake (Fig. 3) appeared to be consistent with this inhibition effect. Because of high elevation, UV light intensity is expected to be much stronger than at sea level (Askew, 2002).
AAP bacteria in anoxic sediments: fossil or light-independent AAP bacteria?
Retrieval of AAP bacteria pufL-M gene sequences from the anoxic and dark sediments of Qinghai Lake was unexpected (Fig. 2). Although the surface sediment of Tokyo Bay was used previously for AAP bacteria isolation work (Yurkov & Beatty, 1998b), AAP bacteria were never isolated successfully. We postulated that two possibilities could explain the presence of the AAP bacteria pufL-M genes in the sediments: (1) they were derived from dead AAP bacteria cells deposited from the overlying water column (fossil DNA); (2) they were derived from active cells (of unknown metabolic pathways) that may have the pufL-M genes. The water column and sediments of Qinghai Lake had some AAP bacteria groups in common, such as the Loktanella-like, Roseobacter-like, Porphyrobacter/Erythrobacter-like, and unknown group-1 sequences. Excluding the unknown group-1, none of the known AAP bacteria in the Loktanella-like, Roseobacter-like, and Porphyrobacter/Erythrobacter-like groups has either been cultured from sediments or shown the ability to survive in anoxic environments, because they all require light for growth. Thus, the AAP bacteria-originated pufL-M gene sequences in the sediments might have been of fossil origin. The fossil DNA of obligate phototrophic algae and their lipid derivatives have been well studied in the context of paleoecology, archaeology, and paleontology (Coolen & Overmann, 1998; Coolen et al., 2004, 2006). However, no similar studies have been performed on AAP bacteria-derived fossil DNA.
Despite the similarity of some cloned gene sequences between the water column and the sediments of Qinghai Lake, multiple AAP bacterial pufL-M gene sequences retrieved from the water–sediment interface (i.e. the unknown group-2, Figs 2 and 3) were not found in the water column. This observation also indicated two possibilities. First, these sequences may have been present in the water column but were overlooked using our sampling scheme. In this scenario, these sequences may represent fossil DNA from the water column (see the discussion above). Second, these AAP bacteria pufL-M gene sequences might be unique to the sediments and possibly derived from indigenous cells. Xiong et al. (2000) and Beatty (2002) proposed that certain purple photosynthetic bacteria might have lost their photosynthetic functions in evolution. According to such a theory, Jiao et al. (2007) speculated that some AAP bacteria species could have lost their photosynthetic genes and gradually developed heterotrophic metabolic pathways. If this evolution pathway were true, AAP bacteria at the transition might have first developed heterotrophic metabolic pathways before they became completely independent of light (i.e. loss of pufL-M genes). The AAP bacteria cells, from which the pufL-M gene sequences in the unknown group-2 originated, could have represented this transition stage. Although these AAP bacteria could still possess the pufL-M genes because they may be deposited from the oxic water column within years (according to a sedimentation rate of 1.25 mm year−1, CAS, 1979), the anoxic and dark environments in the Qinghai Lake sediments would not permit them to depend on light for growth. Such AAP bacteria could have developed a distinct heterotrophic pathway to cope with the conditions in the sediments. However, future work would be necessary for verification of this evolution hypothesis.
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Molecular work performed in this study indicated that AAP bacteria were abundant in saline lakes on the Tibetan Plateau, NW China, with the AAP bacteria percentage levels comparable to those in the oceans. Out of a limited number of environmental factors examined (salinity, pH, DO, conductivity, turbidity, TN, TP, and DIC and DOC), salinity, and pH were found to be potential factors in controlling the AAP bacteria diversity and community structure. Whereas certain AAP bacteria may be preserved as fossil DNA in anoxic and dark lake sediments, others might be able to survive independent of light but may still possess the pufL-M genes.
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This research was supported by National Science Foundation grant EAR-0345307 to H.D., National Science Foundation of China grants (40672079 and 40472064) to B.Y. and H.D., and the 111 Project (No. B07011) of China. We thank Qinglong Wu for TN and TP analyses. We are grateful to three anonymous reviewers whose constructive comments helped improve the quality of the manuscript.
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- 1972) Control of synthesis of reaction center bacteriochlorophyll in photosynthetic bacteria. Photochem Photobiol 15: 209–225. & (
- 2005) PCR-induced sequence artifacts and bias: insights from comparison of two 16S rRNA clone libraries constructed from the same sample. Appl Environ Microb 71: 8966–8969. , , & (
- 2003) Aerobic anoxygenic photosynthesis in Roseobacter clade bacteria from diverse marine habitats. Appl Environ Microb 69: 5051–5059. , , & (
- 2002) Work at high altitude and oxidative stress: antioxidant nutrient. Toxicology 180: 107–119. (
- 2002) On the natural selection and evolution of the aerobic phototrophic bacteria. Photosynth Res 73: 109–114. (
- 2002) Unsuspected diversity among marine aerobic anoxygenic phototrophs. Nature 415: 630–633. , , , , , , , & (
- CAS (1979) Comprehensive Survey Report of Qinghai Lake. Scientific Publishing House, Beijing.
- 2007) Polyphyletic photosynthetic reaction centre genes in oligotrophic marine Gammaproteobacteria. Environ Microbiol 9: 1456–1463. , , , , , , & (
- 1998) Analysis of subfossil molecular remains of purple sulfur bacteria in a lake sediment. Appl Environ Microb 64: 4513–4521. & (
- 2004) Evolution of the methane cycle in Ace Lake (Antarctica) during the Holocene: response of methanogens and methanotrophs to environmental change. Org Geochem 35: 1151–1167. , , , , , & (
- 2006) Ancient DNA derived from alkenone-biosynthesizing haptophytes and other algae in Holocene sediment from the Black Sea. Paleoceanography 21. PA1005, DOI: DOI: 10.1029/2005PA001188. , , , , & (
- 2006) Aerobic anoxygenic phototrophic bacteria in the Mid-Atlantic Bight and the North Pacific Gyre. Appl Environ Microb 72: 557–564. , & (
- 1999) Phylogenetic analysis of particle-attached and free-living bacterial communities in the Columbia river, its estuary, and the adjacent coastal ocean. Appl Environ Microbiol 65: 3192–3204. , & (
- 1993) Phylogenetic diversity of aggregate-attached vs. free-living marine bacterial assemblages. Limnol Oceanogr 38: 924–934. , & (
- 2007) Geomicrobiological processes in extreme environments: a review. Episodes 30: 202–216. & (
- 2006) Microbial diversity in sediment of saline Qinghai Lake, China: linking geochemical controls to microbial ecology. Microb Ecol 51: 65–82. , , , , , & (
- 1995) Structure, molecular organization and biosynthesis of membranes of purple bacteria. Anoxygenic Photosynthetic Bacteria (BlankenshipRE, MadiganMT & BauerCE, eds), pp. 231–257. Kluwer Academic Publishers, Dordrecht, the Netherlands. & (
- 2006) Real-time PCR for quantification of aerobic anoxygenic phototrophic bacteria based on pufM gene in marine environment. J Exp Mar Biol Ecol 329: 113–121. , , & (
- 2006) Sandarakinorhabdus limnophila gen. nov., sp. nov., a novel bacteriochlorophyll a-containing, obligately aerobic bacterium isolated from freshwater lakes. Int J Syst Evol Micr 56: 847–854. & (
- 1989) Action spectra for inhibition by light of accumulation of bacteriochlorophyll and carotenoid during aerobic growth of photosynthetic bacteria. Plant Cell Physiol 30: 471–477. & (
- 2006) Microbial diversity in water and sediment of Lake Chaka: an athalassohaline lake in northwestern China. Appl Environ Microb 72: 3832–3845. , , , , & (
- 2007) Microbial response to salinity change in Lake Chaka, a hypersaline lake on Tibetan Plateau. Environ Microbiol 9: 2603–2621. , , , , , & (
- 2008) Dominance of putative marine benthic archaea in Qinghai Lake, northwestern China. Environ Microbiol 10: 2355–2367. , , , , , & (
- 2006) Time series observation based infrared epifluorescence microscopic (TIREM) approach for accurate enumeration of bacteriochlorophyll-containing microbes in marine environments. J Microbiol Meth 65: 442–452. , & (
- 2007) Distinct distribution pattern of abundance and diversity of aerobic anoxygenic phototrophic bacteria in the global ocean. Environ Microbiol 9: 3091–3099. , , , , , & (
- 1990) The Standard Methods for Observation and Analysis of Lake Eutrophication, 2nd edn. China Environmental Science Press, Beijing, China (in Chinese). & (
- 2003) Remarkable diversity of phototrophic purple bacteria in a permanently frozen Antarctic lake. Appl Environ Microb 69: 4910–4914. , , , & (
- 2003) Isolation and characterization of Erythrobacter sp. strains from the upper ocean. Arch Microbiol 180: 327–338. , , , , , , , & (
- 2000) Bacterial photosynthesis in surface waters of the open ocean. Nature 407: 177–179. , , & (
- 2001) Contribution of aerobic photoheterotrophic bacteria to the carbon cycle in the ocean. Science 292: 2492–2495. , , , , , , , , & (
- 2007) High abundances of aerobic anoxygenic photosynthetic bacteria in the South Pacific Ocean. Appl Environ Microb 73: 4198–4205. , , , , , , & (
- 2008) Distribution of aerobic anoxygenic phototrophs in temperate freshwater systems. Environ Microbiol 10: 1988–1996. , , & (
- 2002) Determination of bacterial load by real-time PCR using a broad range (universal) probe and primer set. Microbiology 148: 257–266. , , & (
- 1997) Horizontal transfer of genes coding for the photosynthetic reaction centers of purple bacteria. J Mol Evol 45: 131–136. , , & (
- 2005) Roseobacter-like bacteria in Red and Mediterranean Sea aerobic anoxygenic photosynthetic populations. Appl Environ Microb 71: 344–353. , , , & (
- 2004) Representative freshwater bacterioplankton isolated from Crater Lake, Oregon. Appl Environ Microb 70: 6542–6550. , & (
- 1999) Phylogenetic differences between particle-associated and planktonic ammonia-oxidizing bacteria of the beta subdivision of the class proteobacteria in the northwestern Mediterranean Sea. Appl Environ Microb 65: 779–786. , , & (
- 2005) Wide-ranging abundances of aerobic anoxygenic phototrophic bacteria in the world ocean revealed by epifluorescence microscopy and quantitative PCR. Limnol Oceanogr 50: 385–393. & (
- 2001) Alpha- and beta-proteobacteria control the consumption and release of amino acids on lake snow aggregates. Appl Environ Microb 67: 632–645. , , , & (
- 1995) Analyses of dissolved organic carbon in seawater: the JGOFS EqPac methods comparison. Mar Chem 48: 91–108. , , , , , & (
- 2002) Final dissolved organic carbon broad community intercalibration and preliminary use of DOC reference materials. Mar Chem 77: 239–253. , , , , & (
- 2005) Paleoclimate changes in the Qinghai Lake area during the last 18,000 years. Quatern Int 136: 131–140. , , & (
- 2006) Distribution of planktonic aerobic anoxygenic photoheterotrophic bacteria in the northwest Atlantic. Limnol Oceanogr 51: 38–46. , , , & (
- 1992) Inhibition of accumulation of bacteriochlorophyll and carotenoids by blue light in an aerobic photosynthetic bacterium Roseobacter denitrificans, during anaerobic respiration. Plant Cell Physiol 33: 1171–1174. , , & (
- 2005) Aerobic anoxygenic photosynthesis genes and operons in uncultured bacteria in the Delaware River. Environ Microbiol 7: 1896–1908. & (
- 2007) Aerobic anoxygenic phototrophic bacteria attached to particles in turbid maters of the Delaware and Chesapeake estuaries. Appl Environ Microb 73: 3936–3944. & (
- 2008) Diversity and distribution of ecotypes of the aerobic anoxygenic phototrophy gene, pufM, in the Delaware estuary. Appl Environ Microb 74: 4012–4021. & (
- 2004) Carbon dioxide degassing and inorganic carbon export from a marsh-dominated estuary (the Duplin River): a marsh CO2 pump. Limnol Oceanogr 49: 341–354. & (
- 1996) What future for saline lakes? Environment 38: 13–39. (
- 2006) Bacterioplankton community composition along a salinity gradient of sixteen high-mountain lakes located on the Tibetan Plateau, China. Appl Environ Microb 72: 5478–5485. , , , & (
- 2000) Molecular evidence for the early evolution of photosynthesis. Science 289: 1724–1730. , , , & (
- 1998a) Isolation of aerobic anoxygenic photosynthetic bacteria from black smoker plume waters of the Juan de Fuca Ridge in the Pacific Ocean. Appl Environ Microb 64: 337–341. & (
- 1998b) Aerobic anoxygenic phototrophic bacteria. Microbiol Mol Biol R 62: 695–724. & (
- 2002) Diversity, distribution and physiology of the aerobic phototrophic bacteria in the mixolimnion of a meromictic lake. FEMS Microbiol Ecol 40: 191–204. , , , , , & (
- 2005) Putative novel photosynthetic reaction centre organizations in marine aerobic anoxygenic photosynthetic bacteria: insights from metagenomics and environmental genomics. Environ Microbiol 7: 2027–2033. & (
- 2007) Assessing diversity and biogeography of aerobic anoxygenic phototrophic bacteria in surface waters of the Atlantic and Pacific Oceans using the Global Ocean sampling expedition metagenomes. Environ Microbiol 9: 1464–1475. , , , , , & (
- 2007) Dynamics of aerobic anoxygenic phototrophic bacteria in the East China Sea. FEMS Microbiol Ecol 61: 459–469. & (