Effects of water stratification and mixing on microbial community structure in a subtropical deep reservoir.

Microorganisms play pivotal roles within aquatic ecosystems, affecting their structure, functioning and services. However, little is known about the effects of water stratification and mixing on the aquatic microbial community dynamics in subtropical reservoirs. In this study, we explored vertical and seasonal patterns of microbial diversity in the Dongzhen Reservoir (southeast China). Quantitative PCR, quantitative RT-PCR, and 454 pyrosequencing were used for an in-depth characterization of the bacterial community across time (every three months for one year) and space (five different water depths). Our results indicated that thermal and oxygen stratification shaped the phylogenetic composition of microbial communities in the reservoir. There were significant differences in physical, chemical and microbiological parameters between epilimnion and hypolimnion (P < 0.05). The RNA: DNA ratios were significantly lower in epilimnion and metalimnion but rapidly increased in hypolimnion (P < 0.05), suggesting that microorganisms were more active at low temperatures, low dissolved oxygen concentrations and high TN/TP ratios. Redundancy analysis and pathway analysis revealed a complex interplay of various environmental and biological factors by explaining the spatiotemporal variations in bacterial communities. Adaptive reservoir management strategies should consider carefully the effects of water stratification and mixing, together with the distribution patterns of aquatic microorganisms.

Subtropical deep reservoirs are typically characterized by warm monomictic waters showing thermal stratification throughout the year, except for a short mixing period in winter12. During stratification, surface waters (epilimnion) show higher light intensity, temperatures and dissolved oxygen concentrations in comparison to deep waters (hypolimnion). The upper and lower water layers are separated by the lacustrine interface zone - the metalimnion3. During a mixing event after a long period of stratification, nutrients, sulfide, and other dissolved constituents are conveyed to the surface waters, potentially triggering eutrophication processes with direct consequences for ecosystem health status (e.g. algal blooms, odors and fish kills)4. Moreover, these contrasting conditions influence the entire aquatic ecosystem functioning5. Stratification has important implication for phytoplankton succession, fisheries management, and water supply quality. To prevent the occurrence of excessive nutrient loading, artificial destratification systems are sometimes utilized, but without consistent water quality improvements6.

The microbially-driven self-purification processes occurring within the oxygen minimum zone are unquestionably more effective in removing the nutrient excess7. In addition, bacteria utilize a wide range of organic compounds (e.g. humic substances) as electron donors for anaerobic respiration, and this, in turn, could lead to increased release of nutrients from sediments under hypoxic conditions8. Thus, understanding the spatial and temporal heterogeneity and environmental factors that drive the microbial community structuring in reservoirs is essential for developing effective water quality management approaches9.

Microorganisms are well known to serve as the principal producers and decomposers, and play a pivotal role in maintaining freshwater ecosystem health10. Several physical, chemical, and biological variables are known to influence the microbial community composition1112. Previous studies showed that the vertical dynamics of the phytoplankton was related to the water column-mixing regime13. There appeared to be a subtle interaction between inflows, water column stability, the periodic overturns and the occurrence of the dominant species14. While for bacterial community, habitat heterogeneity and seasonal changes can also contribute to community patterns15.

Stratification and mixing periods provide a unique opportunity to explore bacterial community responses to both spatial and temporal changes in the environment16. Thus, thermal stratified reservoirs represent an ideal system in which to investigate physical and chemical drivers of bacterial community structuring. Previous studies reported major differences in physical and chemical conditions across thermal layers of stratified lakes (epilimnia and hypolimnia) and each layer is known to harbor different bacterial communities17. Recently, the rapid development of molecular biological technique has provided powerful tools to specifically explore the aquatic microbial diversity1819.

In this study, a high-throughput sequencing using sequencing-by-synthesis technology was applied as a new approach to exhaustively interpret phylogenetic diversity patterns in microbial communities during stratification and mixing periods. We hypothesized that physical and chemical variables would affect the bacterioplankton diversity at varying extent, and such effects would vary with habitat heterogeneity. Accordingly, our objectives were (i) to examine the effect of water mixing and stratification on the aquatic bacterial diversity, abundance, activity in a subtropical deep reservoir; (ii) to investigate whether the different genera of bacterioplankton coexist together or apart from each other in the different seasons and water depths; and (iii) to investigate the relations between the bacterial community structure and environmental driving factors across time and space.

Methods

Study site, sample collection and nucleic acid extraction

Dongzhen Reservoir (25°29′ N, 118°59′ E) is located in Putian city, southeast China. The reservoir was built in 1960 with a drainage area of 321 km2 and a total storage capacity of 435 million m3. The sampling station is located in the main lacustrine zone close to the dam where the depth is about 36 m throughout the year. Samples were collected every three months, in October 2011 (autumn), January 2012 (winter), May 2012 (spring), and July 2012 (summer) at five different depths (0, 10, 20, 26 and 33 m), respectively. Each water sample (1 liter with three replications at each depth, maintained at the temperature of 4°C) was immediately sent to the laboratory and filtered onto 0.22-μm pore size polycarbonate membranes (47 mm diameter, Millipore, USA) for the DNA and RNA extraction. The filters were frozen at −80°C until DNA/RNA extraction. Total DNA was extracted from the 0.22-μm filters using a FastDNA spin kit (MP Biomedicals, USA) according to the manufacturer's instructions. Total RNA was extracted from the membranes using the E.Z.N.A. total RNA kit II (Omega Bio-Tek, USA) following the manufacturer's instructions. After the extraction procedure, RNA was transcribed into complementary DNA (cDNA) using the Takara OneStep RT-PCR kit Version 2.0 following the manufacturer's instructions. Reverse transcription was performed as a 15 min reaction at 37°C terminated by 5 s incubation at 95°C. Purified DNA and cDNA were stored at −80°C until further use.

Physical and chemical analysis

Water temperature, dissolved oxygen (DO), pH, chlorophyll-a (Chl-a) and electrical conductivity (EC) were measured in situ at 1-m increments using a multiparameter water quality analyzer (Hydrolab DS5, Hach, USA). Total nitrogen (TN) was determined using a Shimadzu TOC-VCPH analyzer (Shimadzu, Japan). Ammonium nitrogen (NH4-N), nitrite and nitrate nitrogen (NOx-N) and phosphate phosphorus (PO4-P) were measured with a Lachat QC8500 Flow Injection Analyzer (Lachat Instruments, USA). Total phosphorus (TP) was analyzed by spectrophotometry after digestion. The water column was defined as thermally stratified if temperature difference exceeded by 1°C within 1 m depth at the metalimnion20.

Quantitative PCR and RT-PCR

PCR amplification of 16S rRNA genes was performed to prepare the quantitative PCR standard curve. The 50-μl PCR mixture contained 1 μl of the primer set (25 pmol each), 0.5 μl (1.25 U) of Ex Taq DNA polymerase (Takara Bio, Japan), 5 μl of Ex Taq buffer, 4 μl of deoxyribonucleotide triphosphate (dNTP) mixture (2.5 mM each), 100 ng of DNA template, and 33.5 μl of ddH2O. The primer were 341F (5′- CCTACGGGNGGCWGCAG -3′) and 515R (5′- ATTCCGCGGCTGGCA -3′)21. PCR was performed in the following thermal cycles: initial denaturation at 94°C for 5 min; 25 cycles at 94°C for 30 s, 51°C for 30 s and 72°C for 60 s; and a final extension at 72°C for 10 min. The purified PCR products (Promega, USA) were ligated into the pMD18-vector (Takara Bio, Japan) and transformed into Escherichia coli DH5α competent cells (Takara Bio, Japan). The plasmids containing 16S rRNA genes fragments were sequenced using an automated sequencer (ABI3730, USA). Successfully inserted plasmids DNA then were extracted using the MiniPrep kit (Qiagen, Germany) and the plasmid concentrations were determined by spectrophotometry using a BioPhotometer (Eppendorf, Germany). Standards were prepared with triplicate from linearized plasmid serial dilutions containing between 109 and 103 16S rRNA gene copies calculated directly from the concentration of extracted plasmid (Table S1). A standard curve was generated by plotting the threshold cycle values versus log10 of the gene copy numbers. The amplification efficiency (E) was estimated using the slope of the standard curve using the following formula: E = (10−1/slope) − 122. The efficiency of PCR should be between 95% and 105% for further analysis. The quantitative PCR and RT-PCR assays were carried out in a volume of 20 μl include 10 μl SYBR Premix Ex Taq ™, 0.5 μM of each primer, 2 μl of total DNA or cDNA, and RNase-free water. The thermocycling steps of the real-time PCR were run according to the manufacturer's instructions (Takara Bio, Japan). All the measurements were performed in triplicate. In this study, the standard curves with r2 = 0.993 ± 0.002 for DNA and 0.992 ± 0.002 for RNA were used as the reference to calculate the concentrations of environmental 16S rDNA and 16S rRNA, respectively. The efficiency of the PCR amplification was 103.3 ± 2.3% (16S rDNA) and 104.2 ± 0.41% (16S rRNA), respectively. We also compared the ratio of 16S rRNA to 16S rDNA, which is a useful approach to estimate the gene activity of the bacterial community.

454 pyrosequencing and sequence analysis

The total DNA was PCR amplified using primers (357F- CCTACGGGAGGCAGCAG and 926R- CCGTCAATTCMTTTRAGT) targeting regions flanking the variable regions 3 through 5 of the bacterial 16S rRNA gene (V3-V5)2324. Each primer set used for PCR amplification contained an eight base DNA bar code for the multiplexing of samples in the pyrosequencing runs25. The 50-μl PCR mixture contained 1 μl of the primer set (10 μm each), 0.125 μl (5 U/μl) of Ex Taq DNA polymerase (Takara Bio, Japan), 2.5 μl of Ex Taq buffer (20 mM MgCl2), 2 μl of deoxyribonucleotide triphosphate mixture (2.5 mM each, Takara Bio, Japan) and 50 ng of DNA template under the following running conditions: initial denaturation at 94°C for 4 min, 25 cycles of 30 s at 94°C, 45s at 50°C, 1 min at 72°C, and a final elongation step for 8 min at 72°C. PCR products were confirmed using agarose gel electrophoresis and these were subsequently isolated from the gel and purified using a GeneJET™ gel extraction kit (Thermo Fisher Scientific, Germany). All amplicons were pooled in equimolar concentrations, and sent for pyrosequencing on a Roche-FLX+ pyrosequencer at Personal Biotechnology (Shanghai, China). Pyrosequencing reads with more than one ‘N' (undetermined nucleotide) and/or those shorter than 200 nt or longer than 1000 nt were removed. Afterwards, primers and barcodes were checked for completeness. Further, the OTUs which contained only 1 read were not used to avoid possible biases, and read with complete barcode sequence was selected for subsequent analysis. Sequences were quality controlled using the Split_Libraries.py with default settings5. Further, any non-bacterial ribosome sequences and chimeras were removed using Black Box Chimera Check software (B2C2) according to the established procedures26. Sequences were analyzed using QIIME (v1.0) (based on 97% sequence similarity). The OTUs which contained 1 read were not used to avoid possible sequencing error. Taxonomic classification of the reads was performed in the Ribosomal Database Project (RDP) database27. A similarity threshold of 50% in the RDP was applied to assign the reads to the phylum level. The reads of known phyla were further classified into orders5.

All sequence data were deposited in the public NCBI database (http://www.ncbi.nlm.nih.gov/) under the accession number PRJNA233420.

Data statistical analysis

The Shannon-Wiener index (H′) was calculated for the 16S rRNA gene diversity. The H′ was determined with the following equation: H′ = −ΣPlnP. The term P was calculated as follow: P = n/N, where n is the sequence number of individual OTU and N is the sequence number of all OTUs in a community28. The microbial community compositions in different samples were compared using UniFrac based on the RDP database taxonomic classification29. Cluster analysis was used to investigate the phylogenetic composition differences of microbial communities among sites with the program of PRIMER5.0. A group-average linked method was used for Bray-Curtis coefficients among microbial communities in cluster analysis. The normality of the environmental variables and microbial abundance was checked using Shapiro-Wilk test and variables were log(x + 1) transformed to improve normality and homoscedasticity for multivariate statistical analyses. Analysis of variance (ANOVA) was used incombination with Scheffe's F multiple-comparison test to examine differences among the parameters of the sampling sites. Variation partitioning analysis was carried out to assess the individual and combined effects of contextual parameters on changes in bacterial community structure. The gradient length of the longest axis explored by detrended correspondence analysis (DCA) was shorter than 3 SD (standard deviation) units. This indicates that species exhibited linear responses to environmental gradients and thus further analyses were conducted using redundancy analysis (RDA) ordination response models. Environmental variables with variance inflation factors (VIF) < 20 were selected for the following forward selection, and the significance of the conditional effects was detected with 999 Monte Carlo permutations30. The variation partitioning analysis was performed on the basis of RDA and pRDA using the R software package with the vegan library. Directed dependencies between the response variables (bacterial community) and all groups of significant relevant contextual parameters were assessed in one causal model with path analysis31. The RV coefficient was used to derive a correlation matrix between groups of variables. The Chi-square test was used to assess the adequacy between the overall causal model and the original correlation matrix, in which the p-value should not be significant, if the proposed model shows in good agreement with the data. The individual path coefficients indicate the strength of the relation between causal and response variables. The fit of the overall path model was evaluated using the statistical platform R with the vegan and sem packages32.

Results

Spatial and temporal environmental heterogeneity

Dongzhen Reservoir is a typical subtropical warm-monomictic reservoir. The water column was well mixed in winter, whereas the stratification events appeared in spring and lasted until autumn (Figure 1). Interestingly, during stratification, the metalimnion was observed from 2 to 10 m in spring and then dropped to 16 m to 21 m in summer, and then appeared between 24 and 26 m depths in autumn. There were obvious changes in the environmental parameters measured between epilimnion and hypolimnion (Table 1), but little variation was observed during the water mixed period in winter. During stratification, temperature, DO, pH and Chl-a were significantly higher in the epilimnion and rapidly dropping down in the hypolimnion (P < 0.05). The nutrient concentrations were stable in the water column, except for total phosphorus. Specifically, the TN/TP mass ratio was significantly lower in epilimnion (P < 0.01) with mean value of 79.46 ± 16.66 and increased to 165.62 ± 29.89 in hypolimnion. Moreover, the water parameters in summer surface layer (0 m) were different from the other sampling sites; temperature reached the highest value of 31°C, DO oversaturated with highest concentration of 11.56 mg/L, pH showed a strong alkalinity at a value of 10.12 and the TN/TP mass ratio was as low as 24.91. Furthermore, a significant narrow metalimnion was found from 23 m to 24 m in autumn. Within the metalimnion range, temperature decreased from 23°C to 20°C, and DO changed from 3.96 mg/L to 0.24 mg/L (Figure 1).

Figure 1

(A–D) Temperature, dissolved oxygen (DO), pH and chlorophyll-a profiles of Dongzhen Reservoir during one year.

The bottom of the reservoir is shown in grey.

Table 1

Environmental parameters, Shannon-Wiener index, dominant species' relative abundance and copy number of DNA and RNA in the Dongzhen Reservoir

Water layer	Mixing layer (n = 5)	Epilimnion (n = 6)	Metalimnion (n = 3)	Hypolimnion (n = 6)
Temperature (°C)	16.17 ± 0.01a	25.04 ± 1.22b	16.87 ± 0.37a	14.18 ± 0.22c
DO (mg l−1)	8.23 ± 0.07a	6.16 ± 1.41a	2.26 ± 2.04b	2.82 ± 1.07b
pH	7.46 ± 0.02a	7.75 ± 0.58a	6.64 ± 0.14ab	6.34 ± 0.10b
Chl-a (μg l−1)	3.24 ± 0.15a	2.39 ± 0.78a	0.73 ± 0.27b	0.82 ± 0.14b
TN (mg l−1)	3.68 ± 0.17a	2.86 ± 0.53a	3.14 ± 1.10a	4.38 ± 1.17a
NH4-N (mg l−1)	0.10 ± 0.02a	0.18 ± 0.04a	0.13 ± 0.11a	0.20 ± 0.08a
NOx-N (mg l−1)	1.42 ± 0.06a	1.15 ± 0.14a	1.28 ± 0.18a	1.34 ± 0.10a
TP (mg l−1)	0.042 ± 0.008a	0.038 ± 0.004ab	0.026 ± 0.007ab	0.025 ± 0.004b
PO4-P (mg l−1)	0.002 ± 0.001a	0.009 ± 0.004a	0.014 ± 0.011a	0.011 ± 0.005a
TN/TP mass ratio	100.70 ± 116.94ab	79.46 ± 16.66a	120.99 ± 37.32ab	165.62 ± 29.89b
Shannon-Wiener index	4.00 ± 0.06ab	3.77 ± 0.13a	4.16 ± 0.04b	4.18 ± 0.09b
Actinobacteria (%)	0.706 ± 0.012a	0.625 ± 0.017b	0.629 ± 0.015b	0.589 ± 0.020b
Proteobacteria (%)	0.139 ± 0.006a	0.183 ± 0.023a	0.204 ± 0.036a	0.216 ± 0.014a
Cyanobacteria (%)	0.075 ± 0.004a	0.045 ± 0.025ab	0.033 ± 0.020ab	0.052 ± 0.020b
Unknown bacteria (%)	0.038 ± 0.001a	0.039 ± 0.008a	0.052 ± 0.006ab	0.059 ± 0.006b
Copy number of DNA (l−1)	(1.14 ± 0.14) × 1010a	(7.92 ± 1.60) × 1010b	(1.06 ± 0.14) × 1011c	(4.45 ± 0.51) × 1010b
Copy number of RNA (l−1)	(6.58 ± 0.16) × 1011a	(3.89 ± 0.72) × 1011b	(2.80 ± 0.60) × 1011b	(8.36 ± 1.36) × 1011c
RNA/DNA ratio	6.31 ± 1.70a	10.59 ± 2.85a	3.01 ± 0.64a	23.17 ± 3.28b

Analysis of variance (ANOVA) was used in combination with Scheffe's F multiple-comparison test to examine differences among the parameters of the sampling sites. Different lower case letters indicate significant differences among the sites.

Data represent mean ± SE.

Bacterial diversity, abundance and activity

Bacterial diversity, abundance and activity differed significantly with depth. The Shannon-Wiener diversity index showed a clear increasing trend from epilimnion (3.77 ± 0.13) to hypolimnion (4.18 ± 0.09) with significant difference (P < 0.05) (Table 1). For the bacterial abundance, the highest copy number of 16S rDNA was found in the metalimnion with an average value of (1.06 ± 0.14) × 1011/L. The highest copy number of 16S rRNA reached (8.36 ± 1.36) × 1011/L in hypolimnion, and there was no difference in 16S rRNA number between epilimnion and metalimnion. Interestingly, the 16S rRNA gene copy numbers in DNA level were generally lower than in RNA level (Figure 2). Further, the RNA: DNA ratios were significantly lower in epilimnion and metalimnion (10.59 ± 2.85 and 3.01 ± 0.64, respectively) and rapidly increased in hypolimnion (23.17 ± 3.28), suggesting that bacterial communities were more active in the low temperature, low dissolved oxygen and high TN/TP ratio water zones (hypolimnion).

Figure 2

Number of 16S rDNA and 16S rRNA copies per liter and RNA: DNA ratio from different water depths (0 m, 10 m, 20 m, 26 m, 33 m) and different seasons (winter, spring, summer, autumn) in Dongzhen Reservoir.

Error bars indicate standard errors of the three replicates samples.

Bacterial community composition

In total, 6068 OTUs with 97% similarity belonging to nine phyla (Actinobacteria, Proteobacteria, Cyanobacteria, Bacteroidetes, Firmicutes, Planctomycetes, Acidobacteria, candidate division WS3 and Verrucomicrobia) were identified. The bacterial community composition differed with depth at the phylum level (Figure 3A). Actinobacteria and Proteobacteria represented the dominant bacterial groups (Figure S1). Actinobacteria showed significantly higher percentages in winter mixing layers (0.706 ± 0.012, P < 0.05) than stratification layers (Table 1). Interestingly, the percentage of Cyanobacteria varied rapidly, with values ranging from 16.6% in the spring surface layer (0 m) to 0.24% in the summer deep layer (33 m). In addition, Bacteroidetes bloomed at the summer surface layer (20.8%) but decreased in the low dissolved oxygen environment (Figure 3A). The cluster analysis based on Bray-Curtis coefficient discriminated four groups at the linkage distance of 79.02% (Figure 3B). The summer surface sample formed a distinct cluster. In fact, the defined groups were closely related according to the sampling seasons and depths. It is worth noting that the bacterial composition of Rhizobiales, Burkholderiales, Rhodospirillales, Methylophilales and Legionellales showed obvious variation associated with water mixing and stratification (Figure S1).

Figure 3

(A) Phylum-level (and Actinobacteria class level) changes in different bacterial composition of Dongzhen Reservoir. Relative abundances of phylotyped reads are shown to their closest match in the Ribosomal Database Project. (B) Cluster analysis of bacterial communities based on the Bray-Curtis similarity of 454 pyrosequencing profiles. The right legend shows color-coding indicating the top 20 most abundant genera in Dongzhen Reservoir.

Relations between microbial community and environmental variables

Among all environmental variables, only statistically significant environmental variables (P < 0.05), including temperature, DO, pH, Chl-a, TN and NOx-N, were selected in the RDA ordination biplot. The first two RDA dimensions by the six parameters explained 81.7% variation of microbial communities (Figure 4A). Temperature, TN + NOx-N and DO + Chl-a + pH separately explained 17.5% (P = 0.001), 7.4% (P = 0.008) and 50.1% (P = 0.001) of the variation, respectively. Microbial communities in summer and autumn (positive values of the RDA x-axis) were relatively different from the winter and spring communities (negative values of the RDA x-axis) (Figure 4A).

Figure 4

(A) RDA bioplot of the distribution of bacterial community and environmental variables in Dongzhen Reservoir. Only statistically significant environmental variables are shown according to Monte Carlo permutation test (P < 0.05). (B) Variation partitioning of bacterial communities into the statistically significant environmental variables.

Pathway analysis was applied to examine microbial communities and reciprocal interactions in their microhabitats. The significance value for the Chi-square test was 0.293, indicating that the proposed model was in good agreement with the data. The goodness-of-fit index and Bentler CFI (Comparative fit index) = 1 indicated a better fit and thus our model was the best fitting model. The Bayesian Information Criterion (BIC) was 28.07, and the minimized value obtaining the better model fit was given (Figure 5). Thus, our results showed that there were demonstrably stark distinctions in physical and chemical conditions across thermal layers in the reservoir.

Figure 5

Final path with structural equation modeling.

The significant value for the Chi-square test is given, assessing whether the model is significantly different from the corresponding correlation matrix. The goodness-of-fit index and Bentler CFI (Comparative Fit Index) indicate the goodness of fit of the model, the best fit would result in a value of 1. The Bayesian Information Criterion (BIC) is another measure of the goodness-of-fit and it is minimized to obtain a better model fit. Numbers on each arrow indicate partial correlation coefficients associated with each causal relationship, and arrow thickness is also proportional to the partial correlation value.

Discussion

Deep reservoirs represent attractive ecosystems in which to explore the influence of habitat heterogeneity on microbial community assembly because of their unique mixing and stratification dynamics16. In this study, we analyzed whether spatial and temporal variations in physical and chemical conditions may be associated with changes in bacterial diversity and community composition. Our results showed that bacterial communities were structurally different between the different water layers of a subtropical deep reservoir. The abiotic and biotic niche diversification, related to water stratification events, could explain the microbial community dynamics across time and space33.

In the Dongzhen Reservoir, we found significant differences in physical (water temperature and DO), chemical (pH, TN, TP and TN/TP ratio) and microbiological (Chl-a, community composition and gene copy number) parameters between epilimnion and hypolimnion (Table 1). Qian et al. (2011) proved that the variation in the microbial communities with depth could be attributable to their adaptations to the various environments5. The thermocline depth is known to be an important factor for microbial community structuring in aquatic ecosystems, particularly for bacterioplankton and phytoplankton groups with limited motility3435. In agreement with previous reports, cluster analysis results clearly showed that the bacterial community composition in the same season was strongly associated with water stratification (Figure 3B). Water stratified isolation, physiological characteristics, and ecological traits could work together to limit bacterioplankton dispersal36. There have been various theoretical predictions for the differential success of microorganism groups to constraints imposed by habitat heterogeneity in freshwater ecosystems, based on competitive abilities for energy availability and nutrient acquisition1637. It was suggested that high local diversity could be maintained under intermediate levels of physical disturbance38. Moreover, low and high levels of disturbance are expected to be less effective in maintaining a high diversity because the former enables competitive exclusion and the latter directly eliminates many species39.

In this study, Actinobacteria, Proteobacteria and Cyanobacteria were the most dominant groups within the analyzed waters. Despite being mainly found in soils40, members of Actinobacteria are recognized as ubiquitous and abundant in lake waters according to recent molecular-based studies10. They can contribute to more than 50% of the total bacteria in surface waters (epilimnion), but often decrease with decreasing oxygen concentrations in the bottom waters (hypolimnion) of lakes and reservoirs41. Within aquatic bacterial communities, Proteobacteria represent the largest and phenotypically most diverse phylogenetic lineage42. Herein, five subdivisions of Proteobacteria were recognized. Alphaproteobacteria, mainly belonging to two genera (Methylocystis and Roseomonas), and Betaproteobacteria, manly belonging to two genera (Acidovorax and Polynucleobacter), were the most abundant groups. Cyanobacteria acting as primary producers were dominant in spring surface waters, but declined sharply in summer and autumn deep water. The ability of Cyanobacteria to perform photosynthesis and nitrogen fixation in the presence of light and oxygen can explain the dominance of this group in the surface waters43.

Our results showed that structural patterns of bacterial communities were related to temperature and nutrient profiles in the stratified water column (Figures 4 and 5). The warmer surface waters re-circulated in the epilimnion, without mixing with the colder and dense waters of the hypolimnion2. Thus, deep waters remained isolated from dissolved oxygen inputs, leading to hypoxic conditions in the hypolimnion. When a mixing event occurred after a long period of stratification, nutrients and other dissolved constituents were conveyed to the upper portion of the water column, leading to water quality deterioration444. Since bacteria drive the organic matter breakdown and nutrient remineralization45, the dominant bacterial metabolic pathways were likely to regulate the solute circulation within different water layers. Temperature differences affected the water density and then led to physical and chemical stratification, which could further contributed to niche differentiation in the water column. Niche differentiation apparently shaped bacterial community and this in turn affected the water quality4647.

Previous researches demonstrated that the water quality may be adversely affected if prolonged stratification occurs in lakes and reservoirs4849. In this scenario, a holistic, ecosystemic, and integrated understanding of the responses of aquatic microbial communities to varying environmental conditions should be considered for establishing appropriate management approaches for water resources protection9.