Introduction

Massive generation of plastic waste has long been considered a worldwide environmental problem. The accumulation of plastic waste and microplastics in the environment can be detrimental to natural ecosystems. Polyhydroxyalkanoate (PHA) is a microbial polymer that can be used in biodegradable plastics, thereby offering a green alternative to nonbiodegradable, petroleum-based plastics. Currently, PHA can be commercially produced using pure cultures of bacteria, such as Cupriavidus necator, Alcaligenes latus, Burkholderia cepacia, and recombinant Escherichia coli1,2. However, the production costs are still high due to the required sterile processes.

Research on PHA production from organic wastewater using mixed microbial cultures has drawn great attention since it can reduce PHA production costs while applying the concept of resource recovery from wastewater. There are several approaches for the enrichment of PHA-accumulating microorganisms in mixed microbial cultures, including creating anaerobic/aerobic, microaerophilic/aerobic, or feast/famine conditions3. At present, feast/famine conditions can support the highest PHA content (89% gPHA/gMLSS) compared to the other approaches4.

The microbial community is an important factor that can affect PHA production in mixed microbial cultures. Previous research has investigated microbial communities in PHA production systems with mixed microbial cultures under feast/famine conditions. Various molecular techniques have been used, such as a 16 S rRNA gene clone library generation5, 16 S rRNA gene amplicon sequencing (MiSeq/HiSeq)6,7, polymerase chain reaction-denaturing gradient gel electrophoresis (PCR-DGGE)8,9,10,11, and fluorescence in situ hybridization (FISH)9,10,12,13,14,15,16,17. However, information on the microbial communities cannot explain which groups of microorganisms actually accumulate PHA in these systems and what roles those microorganisms play. Fortunately, PHA can be stained using fluorescent dyes such as Nile blue A. This technique, supported by FISH, enables us to identify the groups of microorganisms that accumulate PHA. Nevertheless, information on the groups of microorganisms that accumulate PHA and the conditions for PHA accumulation under a feast/famine feeding regime remains limited4,9,10,12,13,16,17. Considering that microbial communities can greatly vary in terms of substrates, operating conditions (e.g., solid retention time (SRT)), seed sludges, and environmental factors (e.g., pH and temperature)13,18, further information on microbial communities and PHA-accumulating microorganisms in mixed microbial cultures is still required. With the current advances in molecular techniques, more complete information on microbial communities can be achieved via next-generation sequencing, which, in combination with FISH and the fluorescence staining technique, can greatly assist in identifying PHA-accumulating microorganisms.

This study aimed to analyze the microbial community in a mixed-culture PHA-accumulating system under feast/famine feeding conditions using 16 S rRNA gene amplicon sequencing (MiSeq) and FISH in conjunction with the fluorescence-based PHA staining technique. The findings from this study improve our understanding of the roles of different groups of microorganisms in PHA accumulation in mixed microbial cultures. In addition, this study expands our knowledge of the microorganisms capable of accumulating PHA in situ in mixed microbial cultures, certain key microorganisms in which may not be individually cultivable.

Materials and Methods

Enrichment of PHA-accumulating microorganisms in an SBR

The seed sludge for the enrichment was taken from an aerobic sequencing batch reactor (SBR) in the wastewater treatment plant of a fruit juice-manufacturing factory. An SBR of 0.3 m × 0.3 m × 0.23 m (width × length × height) with a total wet volume of 20 L was used for the enrichment of PHA-accumulating microorganisms via a feast/famine feeding regime. The SBR was operated at room temperature (27.8 ± 0.83 °C) with an initial mixed liquor suspended solids (MLSS) of 3,000 mg/L. The SBR cycle consisted of five steps: (1) 5 min of synthetic wastewater feeding, (2) 47 h of aeration by air diffusers, (3) 5 min of sludge wastage, (4) 30 min of sludge settling, and (5) 20 min of decanting. The feast/famine conditions occurred in the second step, when aeration was provided. The SBR was operated at an SRT of 10 d. The synthetic wastewater consisted of acetate, 3,000 mg chemical oxygen demand (COD)/L; NH4Cl, 100 mg N/L; KH2PO4, 20 mg P/L; MgSO4, 500 mg/L; CaCl2, 10 mg/L; FeCl3, 10 mg/L; H3BO3, 4 mg/L; CuSO4·5H2O, 2 mg/L; MnCl2·2H2O, 0.3 mg/L; NaMoO4·2H2O, 2 mg/L; ZnSO4·7H2O, 2 mg/L; CoCl2·6H2O, 8 mg/L; NiCl2·6H2O, 2 mg/L; NaHCO3, 50 mg/L, as a pH buffer; and thiourea, 20 mg/L, as a nitrification inhibitor6. The pH was maintained in the 6.5–9.5 range using an automatic pH controller (Alpha 190/200, Thermo Scientific, USA). The COD and MLSS were measured at the beginning and end of each cycle. The COD removal efficiencies (%), which reflect the performance of the SBR in terms of wastewater treatment efficiencies, were calculated from

$$\frac{{{\rm{COD}}}_{0}-{{\rm{COD}}}_{{\rm{e}}}}{{{\rm{COD}}}_{0}}\times 100,$$

where COD0 and CODe are the COD concentrations (mg/L) at the beginning and end of the cycle, respectively. In addition, the COD, MLSS, and PHA levels were measured over time during the 4th, 8th, 12th, 15th, 22nd, and 25th cycles. In these cycles, initial specific rates of substrate utilization (gCOD/gMLSS-h), yields of PHA (gPHA/gCOD), and COD removal efficiencies (%) were estimated. The initial specific rates of substrate utilization (gCOD/gMLSS-h) were estimated during the first 2 h of SBR operation from

$$\frac{1}{{{\rm{MLSS}}}_{0}}[\frac{{{\rm{COD}}}_{0}-{{\rm{COD}}}_{2{\rm{h}}}}{2}],$$

where COD0 and COD2h are the COD levels (mg/L) at the beginning of the cycle and at 2 h, respectively, and MLSS0 is the MLSS (mg/L) at the beginning of the cycle. The yields of PHA (gPHA/gCOD) were calculated from

$$\frac{[(\frac{{ \% {\rm{PHA}}}_{{\rm{\max }}}}{100})\times {{\rm{MLSS}}}_{{\rm{maxPHA}}}]-[(\frac{{ \% {\rm{PHA}}}_{0}}{100})\times {{\rm{MLSS}}}_{0}]}{{{\rm{COD}}}_{0}-{{\rm{COD}}}_{\max {\rm{PHA}}}},$$

where %PHAmax and %PHA0 are the maximum PHA content (% gPHA/gMLSS) and the PHA content (% gPHA/gMLSS) at the beginning of the cycle, respectively; MLSSmaxPHA and MLSS0 are the MLSS values (mg/L) when the PHA content was at the maximum level and at the beginning of the cycle, respectively; and CODmaxPHA and COD0 are the COD levels (mg/L) when the PHA content was at the maximum level and at the beginning of the cycle, respectively.

Analytical methods

For the PHA quantification, sludge samples were centrifuged at 8,000 rpm for 5 min and oven-dried at 80 °C for 24 h. The dried samples were added into a 1:1 (v/v) mixture of chloroform and methanol containing 3% sulfuric acid. These solutions were heated at 80 °C for 3 h for methyl esterification of PHA19. The resulting methyl esters of hydroxybutyrate (HB) and hydroxyvalerate (HV) were measured using gas chromatography with a flame ionization detector (Agilent Technologies) equipped with an HP-INNOWax capillary column (30 m × 0.25 mm id 0.25 µm, Agilent Technologies). Poly(3-hydroxybutyrate-co-3-hydroxyvalerate) containing 12 wt % of HV was used as the PHA standard (Sigma-Aldrich, Co.), and benzoic acid served as an internal standard6. The COD and MLSS values were measured using the closed reflux and gravimetric methods, respectively20. The automatic pH controller monitored the pH values.

Microbial community analysis using 16 S rRNA gene amplicon sequencing

The sludge sample from the SBR cycle that achieved the maximum PHA content was further analyzed for its microbial community using 16 S rRNA gene amplicon sequencing. A DNA extraction kit (FastDNA® Spin Kit for Soil, MP Biomedicals, USA) was used. The v4 region of the 16S rRNA gene was amplified using polymerase chain reactions (PCRs) with the universal primers for bacteria and archaea: 515 F: 5′-GTGYCAGCMGCCGCGGTAA-3′ and 806 R: 5′-GGACTACHVGGGTWTCTAAT-3′21. The PCR conditions were as follows: an initial denaturation at 95 °C for 3 min; 20 cycles of 95 °C for 30 s, 55 °C for 30 s, and 72 °C for 30 s; and a final extension at 72 °C for 5 min. The PCR product was purified using the GF-1 AmbiClean Kit (Gel & PCR, Vivantis Technologies). The purified PCR product was indexed using the Nextera XT Index Kit with 8 cycles of the above PCR conditions. Next, the indexed 16 S rRNA gene amplicon was purified using AMPure XP beads (Beckman Coulter, USA), pooled, and diluted to a final loading concentration of 4 pM. The pooled sample was sequenced on an Illumina MiSeq Sequencer at Omics Sciences and Bioinformatics Center (Chulalongkorn University, Bangkok, Thailand). The quality of the sequences was checked using FASTQC software. Paired-end reads were combined using PEAR22. Assembled reads in which 90% of the bases had quality scores less than 30 or reads shorter than 200 bp were removed using FASTX-Toolkit. The UCHIME method was used to remove chimeric sequences by implementing vsearch1.1.1 with the uchime_ref option against the chimera-free Gold RDP database23,24. Operational taxonomic unit (OTU) picking was conducted using the pick_open_reference_otus.py command with the SortMeRNA method in QIIME 1.9.0. The Greengenes database was used for taxonomic assignments. The sequences that failed to match the references were clustered de novo using SUMACLUST. OTUs with less than 0.1% reads were removed.

Investigation of PHA-accumulating microorganisms

FISH was performed with the PHA staining technique using methods from previous studies4,25,26, with some modifications. A sludge sample (1 mL) from the SBR cycle that achieved the maximum PHA content was collected (the same sample that was used for the 16S rRNA gene amplicon sequencing analysis). The pelleted sample was fixed with 4% paraformaldehyde (SCBT, USA) at 4 °C for 1.5 h or overnight. Equal volumes of phosphate-buffered saline (PBS; 137 mM NaCl, 8.1 mM Na2HPO4·7H2O, 2.68 mM KCl, 1.47 mM KH2PO4; pH 7.2) were used to wash the sludge twice, and the sample was stored at −20 °C in a 1:1 solution in PBS with 99.5% ethanol. The fixed sludge was spotted on MAS-coated glass slides (Matsunami Glass, Osaka, Japan), air-dried, and dehydrated in 50%, 80%, and 99.5% ethanol consecutively for 3 min each. Hybridization solutions (900 mM NaCl, 20 mM Tris/HCl (pH 7.4), 0.01% SDS) were prepared with different formamide concentrations as required for each oligonucleotide probe25. Hybridization solutions containing the different probes and competitors were applied to the slides. The final concentration of each probe in the hybridization buffer was 0.1 pmol/µL. Hybridization was performed at 46 °C for 2–4 h. Excess probe was removed with the appropriate washing buffer by heating at 48 °C for 15 min followed by rinsing with cool dH2O25. The dried biomass was dipped into 1% (w/v) Nile blue A (Sigma-Aldrich, Germany) at 55 °C for 15 min to stain the PHA (blue color) before washing with 8% (v/v) acetic acid solution for 1 min, according to Johnson et al.4. After air-drying, 8 μL of DAPI solution (1 μg/mL, blue) was spotted onto the sample for 15 min and washed off with dH2O to enumerate the total microorganisms.

The oligonucleotide probes were used to determine the PHA accumulation capacity of Alphaproteobacteria, Betaproteobacteria, Gammaproteobacteria and Thauera spp. Table 1 shows the experimental conditions. The probes were synthesized and labeled with Cy3 (red) by Macrogen, Korea. The nonlabeled competitors (BET42a and GAM42a) were used at equimolar concentrations with the target probes. Slow-Fade solution and a cover glass were applied to the dried biomass. Microscopic observation was performed using an Olympus Fluoview FV10i confocal laser scanning microscope (Olympus, Japan). The percentage of total specific bacterial groups (red) was enumerated versus the total number of microorganisms (blue) or PHA-accumulating organisms (yellow). Twenty images were taken for each probe-hybridized sample. Sludge samples without PHA from the initial cycle of this SBR and the nitrifying reactor were used as a negative control for PHA staining for FISH hybridization.

Table 1 Oligonucleotide probes used for FISH in this study.
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Results and Discussion

Enrichment of PHA-accumulating microorganisms in an SBR

PHA-accumulating microorganisms were enriched in the SBR under feast/famine feeding conditions. Figure 1a shows the COD levels in the SBR at the beginning (0 h), in the middle (24 h), and at the end (47 h) of the SBR cycles. The COD levels in the middle and at the end of the cycles were rather close, indicating that the SBR reached famine conditions during every cycle. Figure 1b shows the MLSS in the SBR. The MLSS increased in the middle of the cycles, suggesting biomass growth during the first half of the cycles. On the other hand, the MLSS decreased at the end of the cycles, suggesting biomass decay during the second half of the cycles, consistent with the famine conditions observed based on the COD levels. The average COD removal efficiency for all of the SBR cycles was 92.0 ± 1.9%, which was comparable to typical aerobic treatment processes, suggesting that this system can still effectively serve as a wastewater treatment system.

Figure 1
figure 1

COD (a) and MLSS (b) levels in the SBR: □ at the beginning of the cycle (0 h); ▲ at the middle of the cycle (24 h); ○ at the end of the cycle (47 h).

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Figure 2 shows the COD and MLSS levels in the 4th, 8th, 12th, 15th, 22nd, and 25th cycles in greater detail. According to the COD results, the lengths of the feast/famine conditions were approximately 6 h and 41 h, respectively, which corresponds to a feast/famine ratio of 0.146. This ratio is considered low, which is suitable for the enrichment of PHA-accumulating microorganisms5,15. In addition, Fig. 2 shows the PHA contents in the biomass in the 4th, 8th, 12th, 15th, 22nd, and 25th cycles. In each cycle, the PHA content increased during the feast phase and reached a maximum at approximately 2–4 h. The PHA content gradually decreased during the famine phase, suggesting that PHA was used as the carbon source when the external substrate was depleted. Regarding the PHA composition, the PHA in all of the samples consisted of 100% HB. No HV was detected. This observation is consistent with previous studies that found 100% HB when acetate was used as a substrate for PHA production4,27.

Figure 2
figure 2

COD levels (□), MLSS values (▲), and PHA contents (●) in the 4th (a), 8th (b), 12th (c), 15th (d), 22nd (e), and 25th (f) cycles of SBR operation.

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The initial specific rates of substrate utilization (gCOD/gMLSS-h), maximum PHA contents (% gPHA/gMLSS), and yields of PHA (gPHA/gCOD) in the 4th, 8th, 12th, 15th, 22nd, and 25th cycles are summarized in Table 2. The initial specific rates of substrate utilization appeared to be higher in the latter cycles (12th, 15th, 22nd, and 25th cycles) than in the earlier cycles (4th and 8th cycles). Similarly, the maximum PHA contents in the latter cycles (12th, 15th, 22nd, and 25th cycles) were higher than those in the earlier cycles (4th and 8th cycles). The higher initial specific rates of substrate utilization and the higher maximum PHA contents in the latter cycles were likely due to microbial selection and adaptation to the imposed feast/famine conditions. The average yield of PHA was 0.30 ± 0.06 gPHA/gCOD (~0.45 Cmol PHB/Cmol acetate), which was within the range 0.21–0.60 Cmol PHB/Cmol acetate previously observed by Johnson et al.27.

Table 2 Initial specific rates of substrate utilization (gCOD/gMLSS-h), maximum PHA contents (% gPHA/gMLSS), and yields of PHA (gPHA/gCOD) at different cycles of SBR operation.
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According to the COD, MLSS, and PHA results, feast/famine conditions were successfully established, and PHA-accumulating microorganisms were enriched in the SBR. The maximum PHA content (32.3% gPHA/gMLSS) was achieved in the 12th cycle after 4 h of SBR operation. The sludge sample at that time point was collected for microbial community analysis using MiSeq and for investigation of PHA-accumulating microorganisms using FISH.

Microbial community analysis using 16 S rRNA gene amplicon sequencing

The microbial community in the sludge sample that achieved the maximum PHA content was analyzed using 16S rRNA gene amplicon sequencing (MiSeq). Table 3 shows the results. The relative abundances of different phyla are summarized as percentages in Fig. 3. Proteobacteria, including Betaproteobacteria (51.37%), Gammaproteobacteria (23.44%), and Alphaproteobacteria (13.26%), was the most abundant phylum. Several microorganisms in these three classes of Proteobacteria, such as Cupriavidus necator, Burkholderia cepacia, Alcaligenes latus, Thauera selenatis, Plasticicumulans acidovorans, and Caulobacter crescentus, are known PHA-accumulating microorganisms1,9,28,29. Bacteroidetes (10.15%) was also found in the sludge sample. No microorganisms in this phylum have been reported to accumulate PHA. However, Bacteroidetes species are likely to play a role in protein degradation in the system30,31, and they have been found in activated sludge systems32,33.

Table 3 Microbial community analysis using 16S rRNA gene amplicon sequencing (MiSeq) in the sludge when the PHA content was at its maximum (the 12th cycle of SBR operation), presented as percent relative abundance values.
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Figure 3
figure 3

Microbial community analysis using 16S rRNA gene amplicon sequencing (MiSeq) in the sludge when the PHA content was at its maximum (12th cycle of SBR operation), shown as percent relative abundances.

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Table 4 shows the most abundant families and/or genera in the sludge. Thauera was determined to be the most abundant genus, with a relative abundance of 48.88%. Thauera is a genus in the family Rhodocyclaceae of the order Rhodocyclales of Betaproteobacteria. This organism has been reported to accumulate PHA in mixed microbial culture systems under feast/famine conditions13,16,17,33,34. Despite the different techniques in microbial community analysis, the results are in agreement with those of Lemos et al., who used FISH for microbial community analysis and found that Thauera was dominant at 49.4% and 41.1% of the total bacteria in SBRs fed with acetate under feast/famine conditions at SRTs of 1 d and 10 d, respectively13. Nevertheless, the presence of Thauera does not confirm its in situ capability to accumulate PHA in the system. Alphaproteobacteria, Betaproteobacteria, and Gammaproteobacteria were the dominant groups of microorganisms, and their PHA-accumulating capabilities have been previously reported. Therefore, in situ determination of the PHA-accumulating microorganisms was performed focusing on these groups, as discussed in the following section.

Table 4 The most abundant families and/or genera in the sludge when the PHA content was at its maximum (12th cycle of SBR operation).
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Investigation of in situ PHA-accumulating microorganisms by FISH

FISH was conducted to confirm the roles of Alphaproteobacteria, Betaproteobacteria, and Gammaproteobacteria in PHA accumulation. Based on the PHA accumulation results in the SBR reactor, the most abundant PHA-accumulating sludge was found 4 h into the 12th cycle (32.2% gPHA/gMLSS), as shown in Fig. 2c. This sludge sample was subjected to both 16S rRNA gene amplicon sequencing and FISH analysis. Nile blue A (yellow) and DAPI (blue) were used to stain the PHA content and the chromosomes of all microorganisms, respectively, together with specific oligonucleotide probes labeled with Cy-3 dye (red) for Alphaproteobacteria (ALF1b+ALF968), Betaproteobacteria (BET42a), Gammaproteobacteria (GAM42a), and Thauera (Thau832).

Figure 4 shows examples of fluorescence microscopy images of the mixed culture. For each probe hybridization reaction, 20 images were taken to quantify the proportion of the specific bacterial groups in the total community. Alphaproteobacteria (ALF1b+ALF968), Betaproteobacteria (BET42a), and Gammaproteobacteria (GAM42a) were found at 21.6% (377 out of 1,744 cells), 38.7% (179 out of 462 cells) and 31.2% (113 out of 362 cells), respectively. These results suggest the predominance of Proteobacteria in the SBR reactor, in agreement with the results from 16S rRNA gene amplicon sequencing (MiSeq), which found that the relative abundance of Proteobacteria was up to 88% of the total sequences. Previous studies also observed a predominance of Proteobacteria in mixed PHA-producing microbial systems16,17,34. The proportion of Betaproteobacteria was slightly higher than those of Gammaproteobacteria and Alphaproteobacteria, as also determined from the MiSeq results. However, FISH is based on manual microscopic observation, and the number of detected cells was much lower than the MiSeq result; therefore, FISH was regarded as semiquantitative method.

Figure 4
figure 4

Fluorescence microscopy images of the mixed culture stained with DAPI (blue) for total microbial cells and Cy3-labeled probe (red) for Alphaproteobacteria (ALF1b+ALF968) (a), Betaproteobacteria (BET42a) (b) and Gammaproteobacteria (GAM42a) (c). The yellow color and arrow indicate the overlay of the Nile blue A stain identifying PHA accumulation in a particular cell.

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Positive Nile blue A staining indicates PHA accumulation. Among the total PHA-accumulating bacteria under each probe hybridization condition, 15.1% (8 out of 53 cells) were associated with Alphaproteobacteria and 33.8% (24 out of 71 cells) with Betaproteobacteria. PHA-accumulating Gammaproteobacteria were not found among the 62 PHA-accumulating bacterial cells. This study indicated that some Alphaproteobacteria and Betaproteobacteria were responsible for PHA accumulation and that accumulation by Betaproteobacteria was the most significant. This study did not identify the role of Gammaproteobacteria in PHA accumulation. Our findings were in contrast with those of Johnson et al.4, who found that a Gammaproteobacterium was the dominant PHA-accumulating microorganism in an SBR fed with acetate operated at an SRT of 1 d. Notably, in our study we chose to use an SRT of 10 d. The differences in SRTs could have effects on microbial communities and PHA-accumulating microorganisms.

Based on our 16S rRNA gene amplicon sequencing analysis, Betaproteobacteria accounted for 51.4% of the total microorganisms in the reactor. Thauera (from betaproteobacterial class) was found at 48.88%. Therefore, we further investigated Thauera species using FISH and Nile blue A staining, as these bacteria might be the dominant strains accumulating PHA.

Probe THAU83235,36 was incorporated to investigate the role of Thauera spp. on PHA accumulation as shown in Fig. 5. This probe was selected because it is capable of detecting 91.3% (379 in total 415 sequences) of Thauera species in the SILVA SSU r132 ribosomal RNA database (TestProbe achieved on September 15, 2019)37. This probe could negligibly bind to other groups (i.e., 3 sequences of uncultured Rhodocyclaceae, 2 Longilinea, 2 Zoogloea, 1 uncultured Deferribacteraceae, 1 SM1A02 Phycisphaeraceae, 1 Azoarcus, 1 uncultured Xanthomonadaceae, and 1 Aminivibrio). Of 176 Nile blue A-stained PHA cells in 20 microscopic fields, 140 cells were bound to the probe THAU832, accounting for 80.3%. This study clearly indicated the ability of Thauera spp. for PHA accumulation in feast/famine mixed-culture SBR feeding with acetate as a main carbon source.

Figure 5
figure 5

(a) Fluorescence microscopy image of the mixed culture stained with DAPI (blue) for total microbial cells, Cy3-labeled probe (red) for Thauera spp. (THAU832), and Nile blue A (yellow) for PHA accumulation. (b) Fluorescence microscopy image of Nile blue A (yellow) staining for PHA accumulation. White arrows indicate PHA-accumulating Thauera spp., and green arrows indicate PHA accumulation by other microorganisms.

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Other studies have also found Thauera to accumulate PHA in mixed microbial cultures under feast/famine feeding conditions13,16,34. Lemos et al., who used FISH for microbial community analysis, found that Thauera was dominant and responsible for PHA accumulation in the system13. Jiang et al. also reported the predominance of Thauera selenetis and Plasticicumulans acidivorans in an SBR system fed with a mixture of acetate and lactate under feast/famine conditions at an SRT of 1 d9. However, Jiang et al. suggested that Thauera sp. was a specialist at lactate conversion, while Plasticicumulans acidivorans was a specialist at acetate conversion9. Ciggin et al. also found that Thauera and Azoarcus were dominant and capable of PHA accumulation in an SBR system fed with acetate under feast/famine conditions at an SRT of 2 d34. Moita and Lemos reported that Thauera, Amaricoccus, and Zoogloea were the dominant microorganisms in an SBR system fed with bio-oil from fast pyrolysis under feast/famine conditions16. In addition, a recent study by Huang et al. found that Thauera was a predominant microorganism in mixed microbial cultures producing PHA, which were fed with mixtures of protein, carbohydrate, and volatile fatty acids, using 16S rRNA gene amplicon sequencing (HiSeq) although the role and contribution of this microorganism to PHA accumulation was not confirmed7.

Despite the large variety of operating conditions, seed sludges, and environmental factors, Thauera has been found in many PHA-accumulating mixed microbial cultures under feast/famine conditions, suggesting that it is a strong competitor and appears to play important roles in PHA accumulation under feast/famine conditions.

In this study, we applied two complementary techniques, namely, 16S rRNA gene amplicon sequencing (MiSeq) and FISH with fluorescence dye-based PHA staining, to systematically identify in situ PHA-accumulating microorganisms in mixed microbial cultures. Further studies should be designed to investigate methods to promote PHA accumulation by Thauera spp.

Conclusions

The mixed microbial culture enriched with acetate in the SBR under feast/famine feeding conditions was able to accumulate a maximum PHA content of 32.3% (gPHA/gMLSS). The results from 16S rRNA gene amplicon sequencing analysis (MiSeq) show that the dominant group of microorganisms in the sludge with the maximum PHA content was Proteobacteria, consisting of Alphaproteobacteria (13.26% of the total sequences), Betaproteobacteria (51.37% of the total sequences), and Gammaproteobacteria (23.44% of the total sequences). Thauera (Betaproteobacteria), a known PHA-accumulating microorganism, was found at a high relative abundance of 48.88% of the total sequences. FISH analysis with fluorescence PHA staining revealed that microorganisms belonging to Alphaproteobacteria and Betaproteobacteria in the sludge were capable of accumulating PHA. Thauera spp. from Betaproteobacteria contributed 80.3% of the total PHA-accumulating cells.