Comparative Analysis of Methanogenic Communities in Different Laboratory-Scale Anaerobic Digesters

Comparative analysis of methanogenic archaea compositions and dynamics in 11 laboratory-scale continuous stirred tank reactors fed with different agricultural materials (chicken manure, cattle manure, maize straw, maize silage, distillers grains, and Jatropha press cake) was carried out by analysis of the methyl coenzyme-M reductase α-subunit (mcrA) gene. Various taxa within Methanomicrobiales, Methanobacteriaceae, Methanosarcinaceae, Methanosaetaceae, and Methanomassiliicoccales were detected in the biogas reactors but in different proportions depending on the substrate type utilized as well as various process parameters. Improved coverage and higher taxonomic resolution of methanogens were obtained compared to a previous 16S rRNA gene based study of the same reactors. Some members of the genus Methanoculleus positively correlated with the relative methane content, whereas opposite correlations were found for Methanobacterium. Specific biogas production was found to be significantly correlating with Methanosarcinaceae. Statistical analysis also disclosed that some members of the genus Methanoculleus positively correlated with the ammonia level, whereas the prevalence of Methanocorpusculum, Methanobacterium, and Methanosaeta was negatively correlated with this parameter. These results suggest that the application of methanogenic archaea adapted to specific feedstock might enhance the anaerobic digestion of such waste materials in full-scale biogas reactors.


Introduction
Anaerobic digestion (AD) of organic matter is widely used in the treatment of agricultural and food wastes as well as industrial and domestic wastewaters. Moreover, the production of biogas from renewable biomass is a substantial way to partially shift from fossil fuels to renewable greenhouse gas-neutral bioenergy in order to mitigate the climate change. Currently, AD is intensively applied for the generation of clean energy and high-quality organic fertilizers from various organic substrates in many countries [1][2][3][4].
The AD process is driven by the activity of complex microbial consortia comprising different functional groups of bacteria and archaea that convert high molecular weight organic compounds into energy-rich methane in the absence of exogenous electron acceptors. The conversion of organic matter into biogas includes four sequential stages: hydrolysis, acidogenesis, acetogenesis, and methanogenesis. The bacterial community converts organic compounds to organic acids, alcohols, hydrogen, and carbon dioxide, whereas methanogenic members of the domain Archaea produce methane using acetoclastic, hydrogenotrophic, and methylotrophic pathways. The syntrophic relationship between bacteria oxidizing organic acids and alcohols and methanogenic archaea is essential for the AD process. Among various microorganisms involved in biogas generation, methanogens are very sensitive to different environmental factors, such as high ammonia, sulfide, and organic acids concentrations, leading to process impairments. Therefore, a detailed understanding of the microbial consortia in biogas reactors is important to fundamentally and practically develop and improve anaerobic digestion processes [5][6][7][8].
2 Archaea Methanogenic archaea involved in various AD processes include the strict hydrogenotrophic orders Methanomicrobiales, Methanobacteriales, and Methanococcales (with the predominance of distinct members of Methanomicrobiales and Methanobacteriales) as well as acetateutilizing representatives of the order Methanosarcinales (with the predominance of members of the two genera Methanosarcina and Methanosaeta). Unlike Methanosaeta species, most Methanosarcina species can additionally use hydrogenotrophic and methylotrophic pathways of methanogenesis [9,10]. Methanosarcina species are able to achieve stable growth at high organic loading rates (OLR) and high levels of ammonium and acetate. In contrast, high ammonium concentrations and elevated acetate levels were reported to suppress the growth of Methanosaeta species [6,11,12]. However, the presence of some ammonia tolerant Methanosaetaceaerelated microorganisms has also been observed [13,14]. Furthermore, an increased activity of Methanosaeta spp. was discovered during shortening the hydraulic retention time (HRT) despite the high levels of organic acids, a result which was additionally supported by stable isotope fingerprinting of the biogas [15,16]. Different hydrogenotrophic methanogens can form close associations with syntrophic acetate-oxidizing bacteria (SAOB; e.g., Clostridium ultunense [17], Syntrophaceticus schinkii [18], and Tepidanaerobacter acetatoxydans [19]) at elevated temperatures or high ammonia levels. However, the diversity of such syntrophic bacteria and such interactions between bacteria and archaea should be further investigated. In addition, another order of methanogens, Methanomassiliicoccales, producing methane by reducing methanol with hydrogen as the electron donor, has been discovered in various anaerobic environments and became a new object for recent investigations [20,21]. Therefore, the knowledge about the archaeal consortia in diverse anaerobic reactor systems is of practical interest in order to comprehensively understand and control the AD process, mitigate process disturbances, and maximize the methane yield.
In a previous study [22], we investigated the effects of substrate type and various process parameters on the bacterial and archaeal community structure using 16S rRNA gene analysis in 11 different reactor systems. However, the rRNA approach applied in our previous work does not completely reflect the actual community composition of methanogenic archaea due to its lower phylogenetic resolution [15,16,23]. Moreover, the relative abundance data obtained by 16S rRNA gene analysis is biased due to the different copy numbers of rRNA operons in various methanogenic taxa (e.g., Methanoculleus: 1 copy; Methanosaeta: 1-2 copies; Methanococcus: 2-4 copies; Methanosarcina: 3 copies; Methanospirillum: 4 copies according to https://rrndb.umms.med.umich.edu/) [24], while mcrA is a single-copy gene in most methanogens (in rare cases, an additional mrt gene encoding an isoenzyme is found in members of Methanobacteriales and Methanococcales). Mcr catalyzes the final step of methanogenesis and is found in the genomes of all methanogenic archaea [25][26][27].
More detailed knowledge on the relations between various reactor parameters (e.g., temperature, pH, OLR, and HRT as well as ammonia and organic acids levels) and the ecophysiology of methanogens involved in AD can help develop new effective tools to stabilize methanogenesis in biogas reactors and improve their efficiency. Thus, the main goal of this study which continues our previous investigations was to estimate the influence of different process parameters on the methanogenic communities involved in the AD of various agricultural materials (chicken manure, cattle manure, maize straw, maize silage, distillers grains, and Jatropha press cake). The composition and dynamics of the methanogenic communities were investigated in laboratoryscale continuous stirred tank reactors (CSTR) targeting the mcrA genes and comparing the results with the archaeal 16S rRNA gene data obtained previously. Correlations between the abiotic process parameters and the structure of the methanogenic communities were additionally investigated.

Laboratory-Scale Biogas Reactors and Analytical
Techniques. The experiment was started after all reactors had been running under stable conditions for at least threefold HRT to ensure steady state conditions. Table S1 (Supporting Information, SI, available online at http://dx.doi.org/10.1155/ 2016/3401272) shows the main process parameters measured at three sampling times during the operating period of the reactors (for more details, see Ziganshin et al. [22]). Briefly, 11 laboratory-scale reactors were operated under mesophilic conditions (37-40 ∘ C) except that reactors R4.5 and R4.6 were changed to thermophilic conditions (55 ∘ C) between the second and the third sampling points. After the second sampling point, both R4.5 and R4.6 were operated at 39 ∘ C for one week, and then the operation temperature was changed to 55 ∘ C at 0.9-1.1 ∘ C/day. Before the third sampling point, both reactors were operated at 55 ∘ C for 6 days. Reactor R3.1 with a working volume of 36.5 L was fed with chicken manure and cattle manure and had a specific biogas potential (SBP) of 290-390 mL g −1 VS depending on the OLR. Reactor R4.5 with a 12-8 L working volume was set up only with cattle manure (SBP: 250-590 mL g −1 VS depending on OLR and temperature), whereas reactor R4.6 with a working volume of 8 L was set up with cattle manure and dried distillers grains with solubles (DDGS) (SBP: 520-540 mL g −1 VS depending on OLR and temperature). Reactor R4.8 with 10 L working volume (SBP: 340-380 mL g −1 VS ) and reactor R4.17 with a working volume of 100 L (SBP: 590-720 mL g −1 VS depending on OLR) were fed with cattle manure and maize silage. The feedstock for reactors R4.13 and R4.14 with 30 L working volume was composed of cattle manure and maize straw (SBP: 330-400 mL g −1 VS depending on OLR); the feedstock for reactors R4.15 and R4.16 with the same volume consisted of cattle manure and extruded maize straw (SBP: 380-410 mL g −1 VS depending on OLR). Reactors R4.19 and R4.20 which had a working volume of 9 L treated Jatropha press cake (SBP: 450-490 mL g −1 VS depending on OLR). Biogas volume, methane content, and pH values were measured every day whereas acid capacity, concentration of volatile fatty acids (VFA), and total ammonium nitrogen (TAN) concentrations Archaea 3 were measured twice per week as previously described (Table  S1) [22]. Samples for community analysis were taken on day 1, day 35, and day 63 of reactor operation.

DNA Extraction and PCR Amplification of mcrA.
DNA extraction and purification were performed using the FastDNA SPIN Kit for soil (MP Biomedicals). DNA was checked for integrity by agarose gel electrophoresis and quantified with a NanoDrop ND-1000 UV-Vis spectrophotometer (Thermo Fisher Scientific). Amplification of the mcrA genes was carried out with the primers mlas (5 -GGT GGT GTM GGD TTC ACM CAR TA-3 ) and mcrA-rev (5 -CGT TCA TBG CGT AGT TVG GRT AGT-3 ) using the PCR protocol described previously [16].

T-RFLP Analysis.
For terminal restriction fragment length polymorphism (T-RFLP) analysis, the reverse primer was labeled at the 5 -end with phosphoramidite fluorochrome-5-carboxyfluorescein. Fluorescently labeled amplicons were purified with SureClean Plus (Bioline) and digested with HaeIII and MspI restriction enzymes (New England Biolabs) in separate reactions. GeneScan-500 ROX (Applied Biosystems) standard was used to obtain molecular sizing of the terminal restriction fragments (T-RFs). Fluorescently labeled T-RFs were sized on an ABI PRISM 3130xl Genetic Analyzer (Applied Biosystems), and peaks < 50 bp and > 500 bp were removed from the subsequent analysis. Theoretical T-RF values of the mcrA amplicons were calculated with NEBcutter V2.0 (http://tools.neb.com/NEBcutter2/) and confirmed experimentally by T-RFLP analysis of corresponding clones. T-RFLP analysis was conducted in triplicate for each restriction analysis to ensure reproducibility. An R script (R version 2.12.2; http://www.r-project.org/) with a cut-off value of six times the standard deviation was used to remove background noise [28]. Multivariate statistical analysis using the vegan package of R (version 3.0.1) was performed on the T-RFLP profiles applying the Bray-Curtis dissimilarity index [29] as described previously [16,22]. Correlations between the abundance of different T-RF and various reactor parameters were analyzed with the R Hmisc package (based on Spearman's rank correlation coefficient).

Cloning and
Sequencing. PCR products were purified with the QIAGEN PCR Purification Kit, and cloning was performed using the QIAGEN PCR Cloning Kit. For each selected reactor, about 50 to 100 mcrA gene positive clones were chosen and screened by T-RFLP analysis to find inserts matching the dominant peaks of the community T-RFLP patterns. Selected clones from each group were sequenced on an ABI PRISM 3130xl Genetic Analyzer. Data were checked for chimeric sequences with Bellerophon (http://comp-bio .anu.edu.au/bellerophon/bellerophon.pl) [30]. Sequences were compared to public databases using BLASTX and BLASTN programs (http://www.ncbi.nlm.nih.gov/BLAST) excluding environmental clone sequences. Phylogenetic trees were calculated with MEGA5 using the neighbor-joining method based on Jukes-Cantor evolutionary distances [31]. The partial mcrA sequences obtained in this study were deposited in the GenBank database (accession numbers KX523626-KX523674).

Methanogenic Community Composition Based on mcrA
Gene Analysis. Methanogenic archaeal community dynamics in reactors were tracked by T-RFLP fingerprinting analysis combined with clone sequencing as a cost-effective method for the identification of methanogenic communities [32]. The highest BLASTX hits of representative mcrA gene clones and their T-RF values obtained with HaeIII and MspI enzymes are summarized in Table S2 (Supplementary Material). The neighbor-joining tree constructed from mcrA nucleotide sequences is shown in Figure 1. The majority of mcrA sequences were closely related to clones from various anaerobic digesters. In general, a good agreement was obtained with both the mcrA and the archaeal 16S rRNA analyses, but the rRNA gene approach missed the representatives of the family Methanobacteriaceae. According to BLASTX hits, various operational taxonomic units (OTUs) were affiliated with the hydrogenotrophic order Methanomicrobiales (Methanoculleus spp., Methanocorpusculum sp., and unclassified Methanoregulaceae), the hydrogenotrophic family Methanobacteriaceae (Methanobacterium spp. and Methanobrevibacter spp.), the acetoclastic/methylotrophic/hydrogenotrophic Methanosarcinaceae (Methanosarcina spp. and Methanomethylovorans sp.), the acetoclastic Methanosaetaceae (Methanosaeta sp.), and the hydrogen-dependent methylotrophic Methanomassiliicoccales order. Figure 2 shows the T-RFLP patterns generated after digestion of mcrA amplicons with HaeIII. Similar results were obtained with MspI (data not shown).
No significant differences were observed in the community structure of reactor R3.1 fed with chicken and cattle manure, when data for both mcrA and 16S rRNA genes were analyzed and compared. Methanogenic community based on the mcrA gene profiles in R3  Table S2, SI) after digestion of mcrA amplicons with HaeIII. Thus, their differentiation in R3.1 was additionally achieved by using MspI analysis in a separate reaction, which indicated the absence of strict acetoclastic methanogens in this reactor. Most of the sequenced mcrA gene clones belonging to Methanoculleus had high similarities to uncultured methanogens and shared 93-100% BLASTX identity with mcrA sequences of Methanoculleus bourgensis [33], Methanoculleus palmolei [34], and Methanoculleus chikugoensis [35] strains (Table S2,  SI). Methanoculleus with T-RF 455/457 was also found in high proportions in all other reactors ( Figure 2). T-RF 214, also 4 Archaea 4.17-2-32      Archaea assigned to the Methanoculleus genus, was detected at notable abundance in reactors fed with Jatropha press cake, cattle manure, and DDGS (mesophilic conditions) as well as cattle manure and maize silage under various operating conditions ( Figure 2). Methanoculleus phylotypes were also found in all reactors when the rRNA gene approach was applied [22]; however, their proportions in the samples varied. The next predominant taxon was the family Methanobacteriaceae with T-RF 464/465, T-RF 468, and T-RF 471. Members of this group were found in all reactors with the exception of R3.1 that operated at high ammonia and VFA levels. The rRNA gene approach missed the family Methanobacteriaceae, whereas analysis of mcrA genes allowed distinguishing the genera Methanobacterium and Methanobrevibacter within the family Methanobacteriaceae ( Figure 2). The mcrA sequence type with T-RF 471 had 94-97% BLASTX identity to mcrA of Methanobacterium formicicum [36], Methanobacterium kanagiense [37], Methanobrevibacter smithii [38], and Methanobrevibacter gottschalkii [39] ( Table S2, [40], Methanosarcina thermophila [41], and Methanosarcina spelaei [42] strains (Table  S2, SI). Methanosarcina with T-RF 489/491 was identified as an important group in reactors R4.13 and R4.14 fed with cattle manure and maize straw. Furthermore, the same phylotype dominated in reactors R4.15 and R4.16 fed with cattle manure and extruded maize straw. However, the relative abundance of Methanosarcina decreased during the operation of these reactors (from 51-56% to 32-40% T-RF abundance in R4.13 and R4.14 and from 59-73% to 47-48% T-RF abundance in R4.15 and R4.16) (Figure 2(b)). A similar trend had been observed from the same samples by using the rRNA gene approach [22], but in different proportions.
T-RF 489/491 (Methanosarcina sp.) was also predominant in reactor R4.5 fed with cattle manure and its relative abundance reached 77% in the second sample (Figure 2(a)). After the second sampling, the temperature in reactor R4.5 was gradually increased to a maximum of 55 ∘ C. This temperature shift was accompanied by a decrease of Methanosarcina sp. to about 34% T-RF abundance and by an increase of Methanoculleus sp. (T-RF 455/457) from 7% up to 37% T-RF abundance. A similar trend had been observed from the same samples with the rRNA gene approach [22]. In case of reactor R4.6 fed with cattle manure and DDGS, the temperature shift to 55 ∘ C contrarily resulted in strong inhibition of Methanoculleus with T-RF 214 and T-RF 455/457 and in the appearance of Methanosarcina with T-RF 489/491 (from 2% to 46% T-RF abundance). In addition, another Methanosarcina with T-RF 125 was mostly observed in all samples from reactors fed with Jatropha press cake (with T-RF abundance of 17-30%), but Methanosarcina with T-RF 489/491 was detected at low T-RF abundance of 2-9% in these reactors (Figure 2(b)).
Based on the mcrA gene analysis, in contrast to the rRNA gene data [22], lower proportions of Methanosaeta (T-RF 175) were observed in the first and second samples from reactor R4.6. OTU with T-RF 175 had 95-96% BLASTX identity to mcrA of Methanosaeta concilii [43]. Methanosaeta representatives were also detected in maize silage-fed reactors (Figure 2) but in much lower proportions compared to the results using the rRNA gene approach [22]. Other archaea of the genera Methanocorpusculum (T-RF 493) and Methanomethylovorans (T-RF 124) were detected in some samples but in low proportions ( Figure 2). OTU with T-RF 493 had 95-99% BLASTX identity with mcrA of Methanocorpusculum aggregans [44] ( Table S2, SI). OTU with T-RF 124 had 96% BLASTX identity with mcrA of Methanomethylovorans thermophila [45] (Table  S2, SI). Figure 3 illustrates the results of a multivariate statistical analysis shown in nonmetric multidimensional scaling (NMDS) plots calculated from the T-RFLP profiles of mcrA amplicons digested with HaeIII. Figure 3(a) demonstrates very distinct community structures in most reactors, and almost all samples from the same reactor clustered more closely to each other with the exception of the two samples from R4.5 and R4.6 taken at higher temperature (55 ∘ C) and samples from R4.8 which were relatively scattered within the NMDS plot. Vectors of process parameters show that the most decisive abiotic factors shaping the methanogenic community structure in reactor R3.1 were high pH and high TAN and VFA concentrations (acetic and isobutyric acids). The community shift after the temperature change from 38 ∘ C to 55 ∘ C was reflected by the data points of the samples obtained from R4.5 and R4.6 as well (Figure 3(a)). In addition, Figure 3(b) shows the NMDS plot demonstrating vectors of single T-RF which shaped the community composition the most.

Discussion
Despite the fact that comparable results were obtained using both approaches, mcrA data additionally allowed the identification of various members of the family Methanobacteriaceae which were missed with the applied 16S rRNA gene-specific primer set in the previous study. Moreover, the relative abundance data based on mcrA gene were less biased compared to the rRNA gene based approach which is impacted by the gene copy number variability.
Based on the analysis of mcrA as well as 16S rRNA genes, the methanogenic community in reactor R3.1 fed with chicken and cattle manure was less diverse compared to the other ten reactors and was dominated by members of the genus Methanoculleus, indicating strong inhibition of the acetoclastic pathway of methanogenesis. The closely related strains are hydrogenotrophic methanogens that can utilize H 2 /CO 2 or formate as methanogenic substrates. The most obvious explanation for the inhibition of acetoclastic methanogenesis in R3.1 (the frequency of members of Methanosarcinaceae never exceeded 1.5%) is the high concentration of TAN and free ammonia nitrogen (FAN) (up to 5.9 g L −1 and 0.74 g L −1 , resp.) accumulated during the reactor operation at increasing OLR (up to 2.84 g VS L −1 day −1 ; Table S1, SI). However, the prevalence of Methanosarcina in reactors utilizing chicken manure as the sole substrate and operating at high TAN/FAN levels was also reported [46,47], indicating that substrate differences and the inoculum used to start the process might have a crucial impact on the development of microorganisms. In addition, reactor R3.1 operated at high levels of VFA (primarily of acetate and propionate, up to 9.9 g L −1 and 4.1 g L −1 , accordingly). Therefore, instead of acetoclastic methanogenesis, an alternative acetate   Fig. S1). Representatives of the genus Methanoculleus were also found in all other reactors fed with distinct agricultural substrates indicating that they are the key players of hydrogenotrophic methanogenesis under various conditions. Other studies also identified the genus Methanoculleus as a widespread methanogen in various biogas reactors (e.g., [23,[50][51][52][53][54]). Methanoculleus bourgensis MS2 T strain sharing high sequence similarity with clone sequences from the T-RF 455/457 group was successfully applied in a previous Archaea 9 bioaugmentation experiment to alleviate the ammonia toxicity effect [55]. A fivefold increase in relative abundance of Methanoculleus spp. and a 31% increase in methane yield were observed in the bioaugmented CSTR compared to the control, indicating that bioaugmentation can help to solve the toxicity problem associated with ammonia overload in biogas reactors operating with nitrogen-rich feedstock.
Members of the family Methanobacteriaceae were found at high levels in all reactors with the exception of reactor R3.1 fed with chicken and cattle manure, indicating the sensitivity of some species to high ammonia and VFA concentrations. The representatives of this family are strict hydrogenotrophic methanogens, growing and forming methane from either H 2 /CO 2 or formate [36,39]. The rRNA gene approach missed the family Methanobacteriaceae, whereas analysis of mcrA genes allowed distinguishing the genera Methanobacterium and Methanobrevibacter within Methanobacteriaceae. Interestingly, Methanobacterium with T-RF 464/465 negatively correlated with TAN level, pH, and CH 4 content ( < 0.001), while Methanobacteriaceae with T-RF 471 only negatively correlated with temperature ( < 0.001). Members of the family Methanobacteriaceae were detected in different anaerobic digesters (e.g., [23,46]) as well as other environments [56] and in parallel with Methanomicrobiales representatives (e.g., Methanoculleus) they were reported to be involved in the SAO process at high ammonia levels (>2.8 g TAN L −1 ) [49]. Therefore, SAO can also be assumed in reactors R4. 19 and R4.20 fed with Jatropha biomass which operated at elevated levels of TAN (3.2-3.8 g L −1 ; Table S1, SI).
The next group, members of which were found at high levels in all biogas reactor systems but in various proportions, was the genus Methanosarcina. The related strains are acetoclastic and methylotrophic methanogens and some can also utilize H 2 /CO 2 as methanogenic substrates. Methanogens of the genus Methanosarcina (T-RF 489/491) were also discovered among T-RF profiles as dominant microorganisms in most samples of reactor R4.5 fed with cattle manure as well as in reactors R4.13, R4.14, R4.15, and R4.16 fed with cattle manure and maize straw. Methanosarcina with T-RF 489/491 started to dominate in reactor R4.6 fed with cattle manure and DDGS after the gradual temperature change from mesophilic to thermophilic conditions. All these reactors operated at medium levels of ammonia (in the range of 1.2-2.0 g L −1 and 0.05-0.14 g L −1 of TAN and FAN, resp.; Table S1, SI). Additionally, another Methanosarcina with T-RF 125 was mostly observed in all samples from reactors R4.19 and R4.20 fed with Jatropha press cake. Reactors R4.19 and R4.20 operated at higher TAN and FAN levels (up to 3.8 g L −1 and 0.29 g L −1 , resp.) compared to all other reactors (with the exception of R3.1; Table S1, SI). This indicates that different methanogenic species even within the same genus can respond differently to ammonia concentrations. Methanosarcina species can perform acetoclastic methanogenesis and have been suggested to act as hydrogen-consuming microorganisms during SAO in reactors operating at high ammonia levels [12,57]. Methanosarcina spp. are found in various environments [56] and reported to achieve stable growth at high OLR and high levels of ammonium in biogas reactors, indicating their tolerance towards different process impairments [12], and therefore they are frequently found in various biogas reactors (e.g., [8,14,47,55,58]).
Other methanogenic archaea exclusively conducting acetoclastic methanogenesis, Methanosaeta spp. [43,59], were also detected in some reactors in this study. TAN concentration was found to be a significant factor for Methanosaeta, the abundance of which was negatively correlated with this key parameter of AD. In addition, lower acetate values were found in reactors R4.6 and R4.8 operated under mesophilic conditions compared to other experiments. It was previously shown that reactors with low concentrations of ammonia and VFA were dominated by representatives of Methanosaetaceae, whereas reactors with high levels of ammonia and VFA were dominated by members of Methanosarcinaceae [6,11].

Conclusions
This study investigated the effect of substrate type and various process parameters on composition and dynamics of methanogenic communities based on mcrA genes in 11 laboratory-scale biogas reactors operated with different agricultural waste materials. A good agreement was found with the 16S rRNA data obtained previously, but the rRNA gene approach missed the family Methanobacteriaceae while the mcrA gene approach allowed more detailed differentiation of methanogenic taxa. Furthermore, the relative abundance data obtained by the mcrA gene gives better results since the 16S rRNA gene data is more biased due to the different copy numbers of rRNA operons in various archaeal taxa. Multivariate statistics revealed that the decisive process parameters shaping the methanogenic community structure in the reactor fed with chicken manure were the high TAN level, pH, and VFA concentration. The present study shows that application of methanogenic communities in biogas reactors adapted to specific feedstock might improve the anaerobic digestion of such waste materials in full-scale biogas reactors.