Jennifer H. Miller
John T. Novak
Amy Pruden- Virginia Tech, Charles E. Via Department of Civil and Environmental Engineering, Blacksburg, VA, USA
Understanding fate of antibiotic resistant bacteria (ARB) vs. their antibiotic resistance genes (ARGs) during wastewater sludge treatment is critical in order to reduce the spread of antibiotic resistance through process optimization. Here, we spiked high concentrations of tetracycline-resistant bacteria, isolated from mesophilic (Iso M1-1—a Pseudomonas sp.) and thermophilic (Iso T10—a Bacillus sp.) anaerobic digested sludge, into batch digesters and monitored their fate by plate counts and quantitative polymerase chain reaction (QPCR) of their corresponding tetracycline ARGs. In batch studies, spiked ARB plate counts returned to baseline (thermophilic) or 1-log above baseline (mesophilic) while levels of the ARG present in the spiked isolate [tet(G)] remained high in mesophilic batch reactors. To compare results under semi-continuous flow conditions with natural influent variation, tet(O), tet(W), and sul1 ARGs, along with the intI1 integrase gene, were monitored over a 9-month period in the raw feed sludge and effluent sludge of lab-scale thermophilic and mesophilic anaerobic digesters. sul1 and intI1 in mesophilic and thermophilic digesters correlated positively (Spearman rho = 0.457–0.829, P < 0.05) with the raw feed sludge. There was no correlation in tet(O) or tet(W) ratios in raw sludge and mesophilic digested sludge or thermophilic digested sludge (Spearman rho = 0.130–0.486, P = 0.075–0.612). However, in the thermophilic digester, the tet(O) and tet(W) ratios remained consistently low over the entire monitoring period. We conclude that the influent sludge microbial composition can influence the ARG content of a digester, apparently as a result of differential survival or death of ARBs or horizontal gene transfer of genes between raw sludge ARBs and the digester microbial community. Notably, mesophilic digestion was more susceptible to ARG intrusion than thermophilic digestion, which may be attributed to a higher rate of ARB survival and/or horizontal gene transfer between raw sludge bacteria and the digester microbial community.
Introduction
Bacterial resistance to antibiotics is a worldwide problem resulting in untreatable infections, death, and escalating healthcare costs. A large body of research has focused on the connection between antibiotic abuse in human medicine and agricultural settings with clinical antibiotic resistance, but the spread of antibiotic resistance continues to be a problem. Thus, the landscape of the war against antibiotic resistance is expanding, with growing attention on environmental reservoirs, such as wastewater treatment plants (WWTPs). In particular, there is interest in the means by which the transfer of antibiotic resistance genes (ARGs) via environmental routes to clinical pathogens can be mitigated (Davison, 1999; Wellington et al., 2013). It is now understood that even non-pathogenic organisms, such as commensals, can be of concern and can serve as a source of ARGs to pathogenic bacteria of clinical significance (Poirel et al., 2002; Rossolini et al., 2008).
WWTPs are of interest not only because they receive wastewater laden with antibiotics, antibiotic resistant bacteria (ARBs), and the ARGs that they carry, but also because they hypothetically create a hot spot for horizontal transfer of ARGs (Dröge et al., 2000; Schlüter et al., 2007) and can elevate ARGs in impacted receiving environments (Storteboom et al., 2010; LaPara et al., 2011). The nutrient-rich, microbially-dense nature of WWTP biomass, in concert with the presence of antibiotics or other selection factors, has been linked with the elevation and persistence of ARGs in activated sludge (Stalder et al., 2013), wastewater effluent (da Silva et al., 2007; Zhang et al., 2009; Luczkiewicz et al., 2010), and land-applied biosolids (Munir and Xagoraraki, 2011; Munir et al., 2011). Early studies focused on tracking specific ARBs or ARGs in wastewater matrices, while mobile genetic elements (e.g., transposons, integrons, and plasmids) have been the subject of more recent attention given their essential role in facilitating transfer of ARGs from the environment to the clinic (Muniesa et al., 2011; Lupo et al., 2012; Moura et al., 2012; Stalder et al., 2012; Ashbolt et al., 2013; Rizzo et al., 2013; Gillings et al., 2014). The prevalence of plasmid-borne ARGs of clinical relevance in WWTPs (Szczepanowski et al., 2009) is of concern and calls for research to establish understanding of the mechanisms governing ARG persistence and proliferation and means by which to limit ARG propagation.
Sludge digestion is of particular interest as a potential means to mitigate the spread of antibiotic resistance, given that it controls the fate of the vast majority of WWTP biomass and ARGs (Munir et al., 2011). Prior studies have collectively measured tetracycline, sulfonamide, erythromycin, and Class 1 integrase genes, which are considered to be key markers of horizontal gene transfer, in mesophilic and thermophilic digestion (Ghosh et al., 2009; Diehl and LaPara, 2010; Ma et al., 2011; Miller et al., 2013). Thermophilic digestion reduced all ARGs to some extent (1–2 log), whereas mesophilic digestion had variable effects on gene levels. Ma et al. (2011) also reported an enhanced removal (2–3 log) of ARGs during thermal hydrolysis pretreatment. However, the concentration of ARGs increased, with the exception of sul1 and tet(G), in the subsequent mesophilic stage. Recent research has focused on metagenomics of ARGs and ARBs in anaerobic digestion (Resende et al., 2014; Yang et al., 2014; Zhang et al., 2015). Prior research suggests that the digester microbial community and the operating conditions play an important role in determining ARG composition and fate. However, the role of the raw sludge influent ARG composition has not previously been examined and has important implications in terms of relative importance of upstream mitigation strategies (e.g., limiting antibiotic use, separating waste streams) vs. digester operation (e.g., maintaining ideal digester microbial community by seeding or selection by temperature or other factors).
It is difficult to measure horizontal gene transfer events in complex environmental matrices (Luby et al., 2016). Rizzo et al. (2013) summarized that there are three types of retrospective evidence of horizontal gene transfer, including association of the ARG with a mobile genetic element, loss of co-location of the insertion site in the host and the acquired ARG, or the lack of similarity between the ARG phylogeny and the ARB phylogeny. Microcosm studies in sediment (Bonot and Merlin, 2010), activated sludge, biofilm, and anaerobic digestion (Merlin et al., 2011) used an increasing ratio of introduced plasmid DNA normalized to ARB chromosomal DNA over time to signify horizontal gene transfer between the introduced ARB and indigenous bacteria. In the present study, evidence of horizontal gene transfer is approached by tracking the fate of a donor ARB by plate culturing and tracking a particular ARG that it carries via quantitative polymerase chain reaction (QPCR) in experimental digesters spiked with the ARB.
The purpose of this study was to examine the effect of elevated influent ARGs originating from influent ARB hosts during mesophilic and thermophilic sludge digestion. A feature of the experimental approach was that the spiked tetracycline-resistant ARBs (designated Iso M1-1 and Iso T10) were isolated from the mesophilic and thermophilic sludge itself and thus presented the opportunity to observe the behavior of native ARBs and their ARGs when elevated in the digester environment. Iso M1-1 was isolated from mesophilic sludge and was identified as a Pseudomonas sp. carrying the tet(G) tetracycline ARG, which was monitored along with tet(W), an ARG not carried by the isolate and representative of the background. Iso T10 was isolated from thermophilic sludge and was identified as Bacillus sp. carrying tet(W) tetracycline ARG. Quantitative polymerase chain reaction (QPCR) of ARGs along with tetracycline-resistant plate counts provided insight into the fate of the isolate and evidence of horizontal gene transfer. To further examine the fates of ARGs under different digester operating conditions, sul1, tet(O), and tet(W), the intI1 gene encoding the integrase enzyme of Class 1 integrons were monitored in influent raw sludge and digested sludge from lab-scale mesophilic and thermophilic digesters. Overall results of this study help support management options for reducing the spread of antibiotic resistance via sludge digestion.
Materials and Methods
Batch Digestion of Tetracycline-Resistant Isolates
Culture Media
Tryptic soy agar (TSA, 40 g/L) was added to reverse osmosis water, dissolved by heating, autoclaved at 121°C for 20 min, and cooled to 55°C in a water bath prior to antibiotic amendment. Filter-sterilized solutions of tetracycline hydrochloride (Sigma Aldrich) and cycloheximide (Sigma Aldrich) were added to the agar at final concentrations of 16 and 200 mg/L, respectively. Agar was mixed at low speed on a stir plate prior to pouring Petri dishes (100 × 15 mm). These plates were used in the isolation of tetracycline-resistant microorganisms from sludge and in monitoring their fate in batch digestion experiments.
Isolation of Tetracycline-Resistant Bacteria
Tetracycline-amended (16 mg/L) TSA plates were inoculated with 100 μL of 1x, 10x, and 100x diluted mesophilic or thermophilic digested sludge and incubated at 37°C for 24 h. After 24 h, individual colonies were aseptically re-streaked on fresh tetracycline-amended TSA plates and incubated again for 24 h. This process was repeated at least 3 times for 5 mesophilic colonies and 13 thermophilic colonies. DNA extracts of all colonies were screened for tet(C), tet(G), tet(O), or tet(W) presence using QPCR because these genes have been associated with wastewater (Storteboom et al., 2010). However, tet(C) and tet(O) were not detected in any colonies. The mesophilic colony labeled Iso M1-1 was positive only for tet(G) and thermophilic colony labeled Iso T10 was positive only for tet(W). Consistent morphology and growth curves were obtained for Iso M1-1 and Iso T10 (6 and 10-h growth times to stationary phase, respectively). Freezer stocks of the isolates were prepared with cultures grown to density, concentrated by centrifugation, rinsed with phosphate buffered saline, re-concentrated, resuspended in tryptic soy broth with 20% glycerol, and stored at −80°C until use.
Cloning and sequencing of the Iso M1-1 16S rRNA gene indicated that the isolate was a Pseudomonas sp. (accession number KC211303.1, 99% of identity Phylum Proteobacteria, Class Gammaproteobacterium) in 20 of the 20 tested clones. The closest match to Iso T10 was Bacillus sp. (accession number KJ5464450.1, 99% of identity, Phylum Firmicutes) in 20 of the 20 tested clones. Cloning used 16S rRNA primers 8F and 1492R and sequencing returned ~640 basepairs spanning the V1 and partial V2 regions. These results suggest that the isolation procedure was successful in isolating only one genus from each sludge.
Batch Digester Preparation
Six hundred mL flasks of tryptic soy broth were each spiked with 1 mL of Iso M1-1 or Iso T10 freezer stock and cultured to late log phase. Cells were harvested by centrifugation of individual flask contents at 10,000 rpm for 10 min and re-suspended and rinsed in phosphate buffered saline (PBS). The rinse step was repeated three times prior to final resuspension of pellets from two flasks per biological replicate in PBS (~30 mL total per biological replicate). The absorbance at 600 nm was measured for a 10x dilution of the concentrated cell suspension. An absorbance of 1.2 approximated a cell density of 108 cells per mL (109 cells per mL in the undiluted suspension). Digested mesophilic or thermophilic sludge (4.5 mL) was aliquoted to sterile plastic disposable culture tubes (100 × 17 mm, Fisher Scientific) and spiked with the concentrated Iso M1-1 or Iso T10 pure culture, respectively. Additional triplicates were unamended and served as control blanks at time zero. Tubes were incubated in a water bath at the test temperature (i.e., 37or 53°C) over a range of time points up to 40 days in order to capture the death/decay curves. Triplicate sample tubes were removed at each time point and immersed in a water/ice bath to quench the temperature reaction. After quenching, plating on tetracycline-amended agar was done immediately and an aliquot of the sample was stored at −20°C for later DNA extraction of an ARG contained within the isolate and a control ARG (not contained within the isolate).
Cell Culturing/Plating
Aliquots (100 μL) of serial 10x dilutions of the original sample were plated immediately on two tetracycline-amended TSA plates and incubated at 37°C for 24 h prior to cell count. Prior to each dilution and plating, culture tubes were vortexed a moderately high speed for 30 s to disengage bacteria from sludge particles.
pH and TS/VS
Total and volatile solids (Method 2540-G) and pH (Method 4500) were analyzed at the start and end of the batch studies as specified in Standard Methods for the Examination of Water and Wastewater (APHA/AWWA/WEF, 1995).
Continuous Feed Digester Study
Continuous Feed Digester Setup
One 15 L, 12-day solids retention time (SRT) thermophilic (53°C) digester and one 10 L, 20-day SRT mesophilic (37°C) digester were operated as control digesters for a series of digestion studies, as reported elsewhere (Miller et al., 2013). In brief, high density polyethylene cone fermenters (Hobby Beverage Equipment Company, Temecula, CA) with nominal volumes of 6.5 gallons (24.6 L) were fed daily with a 70% primary sludge and 30% thickened waste activated sludge mixture from the Christiansburg, Virginia WWTP, which predominantly receives residential wastewater with minimal industrial contribution and no hospital contributions. The mesophilic and thermophilic digesters were originally seeded with digested (37°C) Christiansburg WWTP sludge and laboratory-scale thermophilic (48–57°C) digester material, respectively. Feed to both digesters was diluted with tap water to maintain a consistent influent total solids (TS) of 2.5% and reduce variations in operating parameters (e.g., pH, alkalinity, VFAs, volatile solids reduction). Raw sludge was collected every 4–6 weeks and stored at 4°C to minimize biological activity until fed into the digesters. TS, volatile solids (VS), and pH of the raw sludge were routinely measured over the 9-month study period. A peristaltic pump was used to mix digester contents by recycling headspace gas to the bottom of the cone digester. Evolved gases were collected in 25-L Tedlar bags (SKC, Inc., 84, Pennsylvania). Both digesters were maintained in a 37°C constant temperature room with the thermophilic digester modified with electric heating tape with a temperature controller (Model No. BSAT 101-100, Thermolyne, Dubuque, Iowa) to further elevate the temperature. Miller et al. (2013) reports data associated with control digesters performance monitoring, including total and volatile solids, total alkalinity, pH, gas volume, headspace methane and carbon dioxide, and volatile fatty acids. DNA samples were collected then stored at −20°C for later DNA extraction from feed sludge (after refrigeration, directly prior to feeding), mesophilic control digester effluent, and thermophilic control digester effluent over the 9-month study period. ARGs [tet(O) and tet(W)] were selected for analysis because they are typically associated with wastewater sources (Storteboom et al., 2010) and they have been shown to have variable treatment efficiencies in anaerobic digestion (Diehl and LaPara, 2010; Ma et al., 2011; Miller et al., 2013). intI1 and ARG sul1 were selected for analysis because they are associated with Class 1 integrons (Mazel, 2006), which have been suggested as a relative indicator of antibiotic resistance (Gillings et al., 2014). In the present study, ARG data points that were used to generate previously published bar chart averages of ARG concentration (Miller et al., 2013) are combined with previously unpublished ARG data points and plotted to examine Spearman rho correlations between ARGs concentrations in the raw feed sludge and digester effluents. These correlations provide insight into the influence of the ARG content of raw sludge on the ARG content of digester effluent (biosolids).
Statistics
Sigmaplot 11.0 (2008) was used to calculate Spearman's rho correlation coefficients and P-values (Helsel and Hirsch, 2002) between ARG-16S ratios measured in the raw sludge feed and digester effluent in the continuous feed digester study. If the correlation coefficient was positive, the variables tend to increase together. If the correlation coefficient was negative, the values tend to decrease together. A P < 0.05 was considered significant.
Quantification of ARGs for Batch and Continuous Feed Studies
DNA was extracted from 175 μL of sludge samples using the MagMax Total Nucleic Acid Extraction Kit (Ambion, Life Technologies) according to manufacturer's protocol. Extracted DNA was diluted 50 × to minimize inhibitory effects and stored at −20°C until analysis by QPCR for bacterial 16S rRNA genes, tet(G), tet(W), tet(O), sul1, and intI1. A 10 μL reaction mixture was comprised of 5.0 μ L SsoFast Evagreen Supermix (Bio-Rad, Hercules, CA), 0.8 μL of each 5 μM primer (Table 1), 2.4 μL molecular biology grade water, and 1 μL of DNA template. All samples were quantified in triplicate. Standards (serial dilutions of cloned genes ranging from 101 to 107 gene copies per μL) and a reagent blank (reaction mixture with molecular biology grade water substituted for DNA template) were included in triplicate with each QPCR well plate. Bio-rad CFX Manager 3.0 generated a standard curve of threshold cycle against log gene concentration. Successful standard curves were characterized by R2> 0.98 and amplification efficiency between 90 and 105% and were used to calculate ARG concentration in the diluted sample extract. ARG gene copy number concentration in sludge was calculated by adjusting the diluted sample extract ARG concentration by reduced volume subsequent to DNA extraction (0.3x), dilution of the extract to reduce QPCR inhibitor concentrations (50x), and unit conversion from μL to mL (1000x). The lowest standard on the QPCR curve (10 gene copy numbers (gcn) per μL) was equivalent to 1.5 × 105 gcn per mL digested sludge.
Table 1. Primer sequence and annealing temperature of the QPCR assays.
Results
Fate of Tetracycline Resistant Isolate (Iso M1-1) during Mesophilic Digestion
Tetracycline-resistant CFU and tet(G) were monitored to provide insight into the fate of Iso M1-1 over a 40-day period after it was spiked to batch mesophilic digesters (Figures 1A,B). Because tet(W) was absent in Iso M1-1, it was monitored as a control ARG present in the background digester community. ARG numbers are presented both as gene copy numbers per volume of sludge (Figure 1A) and normalized to background 16S rRNA genes (Figure 1B), as an indicator of the relative proportion of bacteria carrying ARGs and a means to normalize minor variation in DNA extraction efficiency.
Figure 1. Plate count (CFU/ml sludge) and (A) tet(G) and (B) normalized ARG ratios (ARG gcn/16S rRNA) for tet(G) associated with tetracycline resistant bacteria, including Iso M1-1, during mesophilic treatment at 37°C in digested sludge. tet(W) was included as a control gene because it was not associated with Iso M1-1, but was present in the background community. Background line represents the pre-spike concentration in digested sludge.
Tetracycline-resistant CFU were elevated by about 5-log above background (1.3 × 103 CFU/ml) following the initial spike and subsequently decreased over a 5-day period to ~104 CFU/ml, where they remained ~1-log above background for the remainder of the experiment. At these dilution levels, a few different cell morphologies were evident, but it was not possible to distinguish the Iso M1-1 from other background tetracycline-resistant bacteria.
Digester tet(G) content was elevated by about 1.5-log to 2.9 × 107 gcn/ml following the initial spike of Iso M1-1. tet(G) normalized to 16S rRNA ratio was 0.28 in the pure culture preparation just prior to spiking, suggesting that at least 28% of the Iso M1-1 population carried tet(G). The percentage is likely closer to 100% [i.e., all cells carried tet(G)], as Pseudomonas spp. are reported to contain a median number of 4 copies (range is between four and seven copies) of the 16S rRNA gene per cell (Stoddard et al., 2015). The tet(G) content of the background digester community was 9.1 × 105 gcn/ml (Figure 1A). Unlike CFUs, levels of tet(G) did not decrease with time after the initial spike of IsoM1-1 into the batch digesters, but remained ~1–1.5-log above the background throughout the experiment. When normalized to 16S rRNA genes, tet(G) ratios displayed a decreasing trend and returned to background by day 10 (Figure 1B). This is because 16S rRNA genes increased over this same period, which is suggestive of bacterial growth.
In contrast to tet(G), tet(W) was not influenced by the initial spike of Iso M1-1 and remained at or near the background level throughout the experiment (Figure 1A). This was as expected, given that IsoM1-1 does not carry tet(W). The 16S rRNA gene-normalized tet(G) and tet(W) ratios showed similar trends (Figure 1B).
Fate of Tetracycline-Resistant Isolate (Iso T10) during Thermophilic Digestion
Tetracycline-resistant plate counts in initial spiked thermophilic digester microcosms were elevated to 4.0 × 108 CFU/ml (Figure 2), but decreased immediately and returned to slightly above background (7.3 × 102 CFU/ml) within 15 min and remained at ~103 CFU/ml over an additional 40-day monitoring period. Iso T10 contained tet(W), not tet(G) (as carried by Iso M1-1). The tet(W) content of the background digester community was high (ranged 4.0 × 106–1.2 × 107 gcn/ml over the 40-day experiment), resulting in only a slight increase in tet(W) as a result of the spiked Iso T10, which was within the QPCR analytical error range (data not shown).
Figure 2. Plate count (CFU/ml sludge) of tetracycline-resistant bacteria, including spiked Iso T10, during thermophilic treatment at 53°C in digested sludge.
Lab-Scale Semi-Continuous Feed Digester Study
ARG-16S ratios in the 1) feed and ARG-16S ratios in the 2a) thermophilic digester and 2b) mesophilic digester were compared using Spearman's rho correlation analysis. intI1 ratios in the feed sludge were positively correlated to intI1 ratios in both thermophilic and mesophilic digesters (Figure 3). sul1 ratios in the feed sludge were also positively correlated to sul1 ratios in both thermophilic and mesophilic digesters (Figure 4). Interestingly, intI1 and sul1 ratios were positively correlated in thermophilic digesters as well as mesophilic digesters (Figure 5). This is consistent with current understanding that sul1 is typically associated with Class 1 integrons (Mazel, 2006). In contrast, tet(O) and tet(W) ratios in the feed sludge were not correlated to tet(O) or tet(W) ratios in thermophilic or mesophilic digesters (P > 0.05, Figures 6, 7, respectively).
Figure 3. Spearman rho correlation coefficients and P-values for intI1 ARG ratios (normalized to 16S rRNA) in raw sludge feed compared to intI1 ARG ratios in thermophilic and mesophilic digester effluent. A subset of this data (78% of data points) were previously published in Miller et al. (2013) as bar chart ARG concentration averages in a study of the effects of antibiotic concentration on ARGs in digestion or as ARG trends with time as a function of raw sludge storage temperature.
Figure 4. Spearman rho correlation coefficients and P-values for sul1 ARG ratios (normalized to 16S rRNA) in raw sludge feed compared to sul1 ARG ratios in thermophilic and mesophilic digester effluent. A subset of this data (79% of data points) were previously published in Miller et al. (2013) as bar chart ARG concentration averages in a study of the effects of antibiotic concentration on ARGs in digestion or as ARG trends with time as a function of raw sludge storage temperature.
Figure 5. Spearman rho correlation coefficients and P-values for intI1 compared to sul1 ARG ratios in thermophilic and mesophilic digester effluent. A subset of this data (79% of data points) were previously published in Miller et al. (2013) as bar chart ARG concentration averages in a study of the effects of antibiotic concentration on ARGs in digestion or as ARG trends with time as a function of raw sludge storage temperature.
Figure 6. Spearman rho correlation coefficients and P-values for tet(O) ARG ratios (normalized to 16S rRNA) in raw sludge feed compared to tet(O) ARG ratios in thermophilic and mesophilic digester effluent. A subset of this data (75% of data points) were previously published in Miller et al. (2013) as bar chart ARG concentration averages in a study of the effects of antibiotic concentration on ARGs in digestion.
Figure 7. Spearman rho correlation coefficients and P-values for tet(W) ARG ratios (normalized to 16S rRNA) in raw sludge feed compared to tet(W) ARG ratios in thermophilic and mesophilic digester effluent. A subset of this data (75% of data points) were previously published in Miller et al. (2013) as bar chart ARG concentration averages in a study of the effects of antibiotic concentration on ARGs in digestion.
Discussion
Fate of Tetracycline Resistant Isolate (Iso M1-1) during Mesophilic Digestion
The central question to this study is to what extent raw sludge influences the antibiotic resistance level of an anaerobic digester and its effluent? It was observed that both ARBs and ARGs survived in batch mesophilic reactors. The Iso M1-1 ARB and tet(G) ARG associated with this host remained 1-log and 1.5-log above background, respectively, after 40 days of digestion. This finding has important implications for the management of upstream levels of ARBs and ARGs in primary and secondary sludge, suggesting that sludge pre-treatments that aim to minimize ARB in the influent could help reduce the spread of antibiotic resistance from wastewater sources.
Tetracycline-resistant CFUs rapidly declined following spiking of Iso M1-1 in the influent, indicating that they were initially at a level greater than its carrying capacity for the digester community. This is not surprising given that digesters rely on a symbiotic balance among communities of hydrolytic, fermentatative, and methanogenic microorganisms and any one group cannot survive or thrive without the others. However, the 1-log long term increase in tetracycline-resistant CFUs also suggests that the niche filled by Iso M1-1 within the mesophilic digester community was sufficiently large to accommodate a spike in its population. However, the tetracycline-resistant plate count method could not distinguish Iso M1-1 specifically from the background resistant microorganisms. Bearing this in mind, horizontal transfer of tet(G) to other hosts in the digester microbial communities could have contributed to the increase in tetracycline-resistant CFU.
These results may be specific to Iso M1-1, which was native to a digested sludge environment, whereas, exogenous bacteria typically present in raw sludge may have a different fate. To our knowledge, the overlap of ARB survival or microbe composition in raw sludge and digesters has not previously been reported. However, studies examining ARG survival have reported 1- to 2-log reduction of several ARGs relative to raw sludge during thermophilic digestion, while ARG fate reported under mesophilic digestion conditions has been more variable (Ghosh et al., 2009; Diehl and LaPara, 2010; Ma et al., 2011; Miller et al., 2013). These prior studies did not track or quantify specific ARBs or evidence of horizontal gene transfer.
Sequencing of the Iso M1-1 16S rRNA gene indicated that it was a Pseudomonas sp. Pseudomonas are generally characterized as being extremely metabolically diverse with respect to capability of utilizing a wide range of organic compounds as electron donors and carbon sources and as such have been identified as key players in anaerobic digestion (Kummerer, 2009; Zheng et al., 2013). Pseudomonas also tend to be adept at acquiring and disseminating ARGs, with certain multi-antibiotic resistant strains particularly problematic in hospitals (Obritsch et al., 2004). They are also thought to widely carry tetracycline resistance and have been found to house two or more tetracycline ARGs at a time, including tet(G) (Roberts, 2015). The fact that Pseudomonas are typically aerobic organisms, with some using nitrate as an electron acceptor (Madigan et al., 2010), supports the conclusion that they had a relatively narrow niche in the digester community, but were able to horizontally transfer ARGs as spiked levels attenuated. Interestingly, 16S rRNA gene levels lagged in their decline following CFU decline, suggesting that some time is required for the digester community to re-appropriate cell components (DNA) from dead Iso M1-1 cells into new biomass through growth.
Fate of tet ARG during Mesophilic Digestion
As discussed above, tet(G) ARGs were elevated by ~1.5 log in the effluents of the batch mesophilic digesters, presumably originating from the spiked Iso M1-1 known to be carrying it. In addition to survival of a significant fraction of IsoM1-1 cells and horizontal transfer of tet(G) to new hosts, persistence of extracellular tet(G) cannot be completely ruled out (Nielsen et al., 1996; Pietramellara et al., 2009; Dominiak et al., 2011). However, Zhang et al. (2013) quantified extracellular and intracellular DNA composition in livestock waste lagoon sludge and found that extracellular DNA accounted for less than 0.5% of the total DNA in DNA extracts from sludge, indicating that it degrades readily in sludge environments. Assuming similar distribution of DNA in digesters, tet(G) likely existed primarily in the intracellular form.
The maintenance of tet(G) at elevated levels above background combined with a substantial decrease from spiked levels in the CFU plate counts of Iso M1-1 suggest that horizontal gene transfer was likely the primary mechanism of tet(G) persistence. Rizzo et al. (2013) employed a similar culture-based method to assess horizontal transfer of resistance plasmids where growth of donor bacteria and transconjugates on tetracycline-amended agar plates resulted in elevated tetracycline-resistant CFUs when compared with the plates where the donors and recipients were not inoculated together. Merlin et al. (2011) observed similar loss of donor bacteria with a concurrent relative stability of plasmid pB10 DNA in batch mesophilic (35°C) anaerobic digestion experiments and concluded that the ARG plasmid had entered the indigenous background population via conjugative transfer. Interestingly, the initial 5-log increase in tetracycline-resistant CFUs (an increase of ~108 CFU/ml) translated into only 2-log increase in tet(G) (an increase of ~107 gcn/ml) relative to the background. This suggests that the shock of the initial experimental set-up may stimulate Iso M1-1 to expel a portion of the tet(G) that it carried.
tet(G) has a broad host range and is commonly associated with mobile genetic elements, which supports the conclusion that significant horizontal gene transfer contributed to its persistence in the mesophilic digesters. tet(G) is found in Gram negative bacteria and encodes an energy-dependent, membrane-associated efflux protein. Currently, the following genera are known to be capable of carrying tet(G), including Mannheimia, Ochrobactrum, Roseobacter, Salmonella, Acinetobacter, Brevundimonas, Enterobacter, Escherichia, Fusobacterium, Pasteurella, Proteus, Providencia, Pseudomonas, Shewanella, and Vibrio (Roberts, 2015). It is likely that this list is not exhaustive, but limited by the studies investigating the distribution of tetracycline resistance (Roberts, 2005). Gram negative efflux ARGs [including tet(G)] are commonly associated with large, typically conjugative, plasmids that often carry other ARGs (Roberts, 1996). Conjugative plasmids can be highly promiscuous and can transfer between different genera or even domains (Ochman et al., 2000). tet genes have not yet been found on integrons (Roberts, 2005), although tet genes could be located on the same transposon or plasmid as integrons (Stalder et al., 2012).
Fate of Iso T10 and tet ARG during Thermophilic Digestion
In contrast to the mesophilic digestion condition, tetracycline-resistant CFUs returned almost immediately to background following spiking of the corresponding tetracycline-resistant ARB isolated from thermophilic sludge, Iso T10. This suggests that, in contrast to the mesophilic digestion condition, the niche for Iso T10 was not sufficient to accommodate an expanded population. This could be attributed to the fact that mesophilic digestion is characterized by a wider diversity of microorganisms that are able to assimilate, survive, and thrive in the digester environment. Likewise, it has been hypothesized that the extreme thermophilic environment limits available hosts for ARGs and may at least partially explain why thermophilic digesters often are more efficient for tet ARG removal (Diehl and LaPara, 2010; Ma et al., 2011; Miller et al., 2013).
Alternately, the decline in CFUs following the initial spike could be at least partially the result of bacteria entering the viable but non-culturable (VBNC) state. While it was the intent of this study to obtain isolates native to the mesophilic and thermophilic digester environments, spiking of the cultures back into the digestion tubes following several isolation steps could have affected their acclimation state to the digester environment. In particular, the thermophilic environment may have posed a shock to Iso T10, which was isolated and maintained at 37°C prior to spiking. It is also possible that Iso T10, while isolated from thermophilic digested sludge, was not a viable, active, or continuous member of the thermophilic community, but rather a transient microbe that was present during the initial plating of isolates.
Lab-Scale Semi-Continuous Feed Digester Study
The lab-scale digesters afforded the opportunity to observe the influence of raw sludge ARG levels on the ARG content of mesophilic and thermophilic digesters. Over the 9-month period, feed sludge ARG levels of sul1, intI1, tet(O), and tet(W) were monitored and compared with digester effluent concentrations. Consistent with the batch-scale studies, raw sludge ARG ratios of intI1 and sul1 were positively correlated with intI1 and sul1 ARG ratios in both the mesophilic and thermophilic digester effluents (Figures 3, 4, respectively). This phenomenon could be explained by the survival or selective enrichment of influent raw sludge ARBs containing intI1 or sul1 or by horizontal gene transfer between incoming raw sludge bacteria and the digester community. Thus, the semi-continuous feed digester study confirmed that the ARG content of raw sludge influences the ARG content of the digester effluent. Interestingly, the effect was observed for both mesophilic and thermophilic digesters.
There was no correlation of tet(O) and tet(W) ratios in raw sludge and ratios in thermophilic or mesophilic digester effluent (Figures 6, 7). Also, the tet(O) and tet(W) ratios in the thermophilic digester remained consistently low over the entire monitoring period (Figures 6, 7). These results suggest that the thermophilic digester community was relatively immune to transfer or intrusion of these tet ARGs or tetracycline-resistant ARBs.
In this study, raw sludge was stored in a refrigerator (4°C) to minimize biological activity (degradation of organics) prior to feeding to the digesters. Although cold storage has been shown to increase ARG concentrations in biosolids (Miller et al., 2014), the impact of cold storage on the ARB composition of the raw sludge and survivability in digestion has not been investigated. That being said, ARG concentrations reported herein were measured in raw sludge at the time of feeding (i.e., after refrigeration). Ghosh et al. (2009) monitored tet ARG and intI1 in full-scale WWTPs with no cold storage of sludge prior to digestion and the tet ARG and intI1 trends in thermophilic and mesophilic digestion relative to raw sludge are similar to those reported in the present study. That is, tet ARGs had a variable response in mesophilic digestion, whereas levels in thermophilic digestion were reduced by 0.5- to 2-log (Ghosh et al., 2009) and 1- to 2-log (Miller et al., 2013). Ghosh et al. (2009) reported that intI1 levels were lower in mesophilic digested sludge and thermophilic digested sludge compared to raw sludge in two of three samples and three of three samples, respectively. Our work (Miller et al., 2013) has shown a consistent 1- to 1.5-log reduction of intI1 by both mesophilic digestion and thermophilic digestion.
The variable response of different ARGs within the same digester may not be a surprise, considering intI1 is the integrase gene associated with the highly mobile Class 1 integrons and sul1 is often co-located on Class 1 integrons (Paulsen et al., 1993; Zhang et al., 2009). tet(W) and tet(O) are found on plasmid and chromosomes, but have not been found within integron cassettes (Roberts, 2005). Thermophilic digestion may be able to achieve higher ARG content removal with respect to tetracycline genes because of the limited occurrence of tet genes within this particular thermophilic digester community, the incompatibility of the incoming raw sludge bacteria with the thermophilic digestion community for horizontal gene transfer, and/or the harsh environment restricting entrance into the digester community of new ARBs containing tet genes.
These results also suggest that limiting the ARG content of the initial seed community of a thermophilic digester may help limit the ARG content of digester effluent (i.e., biosolids intended for land application) because the microbial community is less prone to intrusion from raw sludge bacteria and horizontal gene transfer, thus retaining its initial ARG signature (or lack thereof). Again, these results highlight the importance of not only horizontal gene transfer, but also host survival. The limited diversity of a thermophilic digester (Wilson et al., 2008) and limiting (high temperature, high ammonia) conditions of a thermophilic digester likely limit opportunities for horizontal gene transfer and limit survival of incoming ARBs.
Implications for ARG Management via Sludge Digestion
The presence of a diverse bacterial, mobile genetic element, and ARG population in activated sludge systems has recently been highlighted by metagenomic studies (Zhang et al., 2011, 2015). The activated sludge environment is characterized by ambient temperatures (10−25°C), rich nutrient and organic loading, dense microbial populations. Similar conditions also exist in mesophilic digestion, albeit with a higher and more closely controlled temperature regime (~37°C). In contrast, thermophilic regimes operate at high temperatures, endogenous conditions, with very high ammonia concentrations. Thermophilic digestion environments have been shown to support a less diverse microbial population than mesophilic digestion (Wilson et al., 2008). Moreover, to gain critical time-temperature requirements for production of Class A biosolids classification, thermophilic digesters are operated with minimum retention times prior to effluent withdrawal and shorter SRTs. This may allow longer times of uninterrupted degradation between raw sludge additions and shorter solids retention times for HGT to occur. These environmental and operating conditions may give thermophilic digestion a competitive advantage over activated sludge or mesophilic digestion in the reduction of ARG content of biosolids. Although, Zhang et al. (2015) reported similar total tetracycline ARG abundance in thermophilic and mesophilic digested sludge in a metagenomic analysis that gave a broad picture of ARG behavior, this statement is supported by our work, along with other QPCR-based studies reporting enhanced reductions of ARGs by thermophilic digestion relative to mesophilic digestion (Ghosh et al., 2009; Diehl and LaPara, 2010; Ma et al., 2011; Miller et al., 2013). Moreover, although horizontal gene transfer continues to be an important mechanism of ARG persistence for genes associated with Class 1 integrons (sul1, intI1), we also report that thermophilic digestion may allow for the reduction of other ARGs [(tet(O), tet(W)] through incoming ARB death and narrowed host range for horizontal gene transfer.
One possibility would be to intentionally seed a digester with ARG-free microorganisms to support an ARG-free effluent (biosolid). However, it is evident that horizontal gene transfer still does occur, particularly with integrons that are typically associated with mobile genetic elements, so that complete reduction of all ARGs may not be possible with ARG-free digester seed alone. Further investigation into pre-treatments designed for complete cell lysis and DNA degradation in raw sludge are warranted for both digestion methods to reduce intrusive ARBs and transformable DNA. It seems plausible that due to the apparent limitations on microbial diversity and the resultant limitations on horizontal gene transfer, that thermophilic digestion could achieve a higher rate of ARG reductions than mesophilic digestion particularly in the face of inefficient pre-treatments. In conclusion, influent ARB and ARG composition and sludge digestion conditions are important for determining the fate of influent ARBs and ARGs and ultimately determining digester effluent ARG content.
Author Contributions
JM conducted the experiments, wrote the original manuscript, and edited the manuscript. AP provided technical oversight and critical manuscript review and editing. All authors discussed the results and implications and commented on the manuscript at all stages.
Funding
This work was supported by National Science Foundation Chemical, Bioengineering, and Transport Systems CAREER award #0852942 and Virginia Tech Institute for Critical Technology and Applied Science seed funding and award TSTS 11–26. JM was supported by the Charles E. Via, Jr. Department of Civil and Environmental Engineering Via Scholarship, Virginia Tech Graduate School Cunningham Fellowship, and Water Environment Research Foundation (WERF) Project U1R12. The findings of this study do not necessarily reflect the views of the supporting entities.
Conflict of Interest Statement
The authors declare that the research was conducted in the absence of any commercial or financial relationships that could be construed as a potential conflict of interest.
Abbreviations
ARG, antibiotic resistance gene; DNA, deoxyribonucleic acid; MRSA, methicillin-resistant Staphylococcus aureus; PBS, phosphate buffered saline; QPCR, quantitative polymerase chain reaction; VBNC, viable but non-culturable; USEPA, United States Environmental Protection Agency.
References
Aminov, R. I., Garrigues-Jeanjean, N., and Mackie, R. I. (2001). Molecular ecology of tetracycline resistance: development and validation of primers for detection of tetracycline resistance genes encoding ribosomal protection proteins. Appl. Environ. Microbiol. 1, 22–32. doi: 10.1128/A.E.M.67.1.22-32.2001
APHA/AWWA/WEF (1995). Standard Methods for the Examination of Water and Wastewater, 19th Edn. Washington, DC: American Public Health Association/American Water Works Association/Water Environmental Federation.
Ashbolt, N. J., Amézquita, A., Backhaus, T., Borriello, P., Brandt, K. K., Collignon, P., et al. (2013). Human Health Risk Assessment (HHRA) for environmental development and transfer of antibiotic resistance. Environ. Health Perspect. 121, 993–1001. doi: 10.1289/ehp.1206316
Bonot, S., and Merlin, C. (2010). Monitoring the dissemination of the broad-host-range plasmid pB10 in sediment microcosms by quantitative PCApplied R and Environmental Microbiology 76, 378–382. doi: 10.1128/AEM.01125-09
da Silva, M. F., Vaz-Moreira, I., Gonzalez-Pajuelo, M., Nunes, O. C., and Manaia, C. M. (2007). Antimicrobial resistance patterns in Enterobacteriaceae isolated from an urban wastewater treatment plant. FEMS Microbiol. Ecol. 60, 166–176. doi: 10.1111/j.1574-6941.2006.00268.x
Davison, J. (1999). Genetic exchange between bacteria in the environment. Plasmid 42, 73–91. doi: 10.1006/plas.1999.1421
Diehl, D. L., and LaPara, T. M. (2010). Effect of temperature on the fate of genes encoding tetracycline resistance and the integrase of class 1 integrons within anaerobic and aerobic digesters treating municipal wastewater solids. Environ. Sci. Technol. 44, 9128–9133. doi: 10.1021/es102765a
Dominiak, D. M., Nielsen, J. L., and Nielsen, P. H. (2011). Extracellular DNA is abundant and important for microcolony strength in mixed microbial biofilms. Environ. Microbiol. 13, 710–721. doi: 10.1111/j.1462-2920.2010.02375.x
Dröge, M., Pühler, A., and Selbitschka, W. (2000). Phenotypic and molecular characterization of conjugative antibiotic resistance plasmids isolated from bacterial communities of activated sludge. Mol.Gen. Genet. 263, 471–482. doi: 10.1007/s004380051191
Ghosh, S., Ramsden, S. J., and LaPara, T. M. (2009). The role of anaerobic digestion in controlling the release of tetracycline resistance genes and class 1 integrons from municipal wastewater treatment plants. Appl. Microbiol. Biotechnol. 84, 791–796. doi: 10.1007/s00253-009-2125-2
Gillings, M. R., Gaze, W. H., Pruden, A., Smalla, K., Tiedje, J. M., and Zhu, Y. (2014). Using the class 1 integron-integrase gene as a proxy for anthropogenic pollution. ISME J. 9, 1269. doi: 10.1038/ismej.2014.226
Hardwick, S. A., Stokes, H. W., Findlay, S., Taylor, M., and Gillings, M. R. (2008). Quantification of class 1 integron abundance in natural environments using real-time quantitative PCR. FEMS Microbiol. Lett. 278, 207–212. doi: 10.1111/j.1574-6968.2007.00992.x
Helsel, D. R., and Hirsch, R. M. (2002). Statistical Methods in Water Resources. Techniques of Water-Resources Investigations of the United States Geological Survey. Book 4, Hydrologic Analysis and Interpretation. Washington, DC: United States Printing Office.
Kummerer, K. (2009). Antibiotics in the aquatic environment – A review – Part II. Chemosphere 75, 435–441. doi: 10.1016/j.chemosphere.2008.12.006
LaPara, T. M., Burch, T. R., McNamara, P. J., Tan, D. T., Yan, M., and Eichmiller, J. J. (2011). Tertiary-treated municipal wastewater is a significant point source of antibiotic resistance genes into Duluth-Superior harbor. Environ. Sci. Technol. 45, 9543–9549. doi: 10.1021/es202775r
Luby, E., Ibekwe, A. M., Zilles, J., and Pruden, A. (2016). Molecular methods for assessment of antibiotic resistance in agricultural ecosystems: prospects and challenges. J. Environ. Qual. 45, 1. doi: 10.2134/jeq2015.07.0367
Luczkiewicz, A., Jankowska, K., Fudala-Ksiazek, S., and Olanczuk-Neyman, K. (2010). Antimicrobial resistance of fecal indicators in municipal wastewater treatment plant. Water Res. 44, 5089–5097. doi: 10.1016/j.watres.2010.08.007
Lupo, A., Coyne, S., and Berendonk, T. U. (2012). Origin and evolution of antibiotic resistance: the common mechanisms of emergence and spread in water bodies. Front. Microbiol. 3:18. doi: 10.3389/fmicb.2012.00018
Ma, Y. J., Wilson, C. A., Novak, J. T., Riffat, R., Aynur, S., Murthy, S., et al. (2011). Effect of various sludge digestion conditions on sulfonamide, macrolide, and tetracycline resistance genes and Class I integrons. Environ. Sci. Technol. 45, 7855–7861. doi: 10.1021/es200827t
Madigan, M. T., Martinko, J. M., Stahl, D., and Clark, D. P. (2010). Biology of Microorganisms. 13th Edn. San Francisco, CA: Benjamin Cummings.
Mazel, D. (2006). Integrons: agents of bacterial evolution. Nat. Rev. Microbiol. 4, 608–620. doi: 10.1038/nrmicro1462
Merlin, C., Bonot, S., Courtois, S., and Block, J. C. (2011). Persistence and dissemination of the multiple-antibiotic-resistance plasmid pB10 in the microbial communities of wastewater sludge microcosms. Water Res. 45, 2897–2905. doi: 10.1016/j.watres.2011.03.002
Miller, J. H., Novak, J. T., Knocke, W. R., and Pruden, A. (2014). Elevation of antibiotic resistance genes at cold temperatures: implications for winter storage of sludge and biosolids. Lett. Appl. Microbiol. 59, 587–593. doi: 10.1111/lam.12325
Miller, J. H., Novak, J. T., Knocke, W. R., Young, K., Hong, Y. J., Vikesland, P. J., et al. (2013). Effect of silver nanoparticles and antibiotics on antibiotic resistance genes in anaerobic digestion. Water Environ. Res. 85, 411–421. doi: 10.2175/106143012X13373575831394
Moura, A., Oliveira, C., Henriques, I., Smalla, K., and Correia, A. (2012). Broad diversity of conjugative plasmids in integron-carrying bacteria from wastewater environments. FEMS Microbiol. Lett. 330, 157–164. doi: 10.1111/j.1574-6968.2012.02544.x
Muniesa, M., Imamovic, L., and Jofre, J. (2011). Bacteriophages and genetic mobilization in sewage and faecally polluted environments. Microb. Biotechnol. 4, 725–734. doi: 10.1111/j.1751-7915.2011.00264.x
Munir, M., Wong, K., and Xagoraraki, I. (2011). Release of antibiotic resistant bacteria and genes in the effluent and biosolids of five wastewater utilities in Michigan. Water Res. 45, 681–693. doi: 10.1016/j.watres.2010.08.033
Munir, M., and Xagoraraki, I. (2011). Levels of antibiotic resistance genes in manure, biosolids, and fertilized soil. J. Environ. Qual. 40, 248–255. doi: 10.2134/jeq2010.0209
Nielsen, P. H., Frolund, B., and Keiding, K. (1996). Changes in the composition of extracellular polymeric substances in activated sludge during anaerobic storage. Appl. Microbiol. Biotechnol. 44, 823–830. doi: 10.1007/BF00178625
Obritsch, M. D., Fish, D. N., MacLaren, R., and Jung, R. (2004). National surveillance of antimicrobial resistance in Pseudomonas aeruginosa isolates obtained from intensive care unit patients from 1993 to 2002. Antimicrob. Agents Chemother. 48, 4606–4610. doi: 10.1128/AAC.48.12.4606-4610.2004
Ochman, H., Lawrence, J. G., and Groisman, E. A. (2000). Lateral gene transfer and the nature of bacterial innovation. Nature 405, 299–304. doi: 10.1038/35012500
Paulsen, I. T., Littlejohn, T. G., Rådström, P., Sundstrom, L., Skold, O., Skurray, R. A., et al. (1993). The 3′ conserved segment of integrons contains a gene associated with multidrug resistance to antiseptics and disinfectants. Antimicrob. Agents Chemother. 37, 761–768. doi: 10.1128/AAC.37.4.761
Pei, R., Kim, S. C., Carlson, K. H., and Pruden, A. (2006). Effect of river landscape on the sediment concentrations of antibiotics and corresponding antibiotic resistance genes (ARG). Water Res. 40, 2427–2435. doi: 10.1016/j.watres.2006.04.017
Pietramellara, G., Ascher, J., Borgogni, F., Ceccherini, M. T., Guerri, G., and Nannipieri, P. (2009). Extracellular DNA in soil and sediment: fate and ecological relevance. Biol. Fertil. Soils 45, 219–235. doi: 10.1007/s00374-008-0345-8
Poirel, L., Kämpfer, P., and Nordmann, P. (2002). Chromosome-encoded ambler class A beta-lactamase of Kluyvera georgiana, a probable progenitor of a subgroup of CTX-M extended-spectrum beta-lactamases. Antimicrob. Agents Chemother. 46, 4038–4040. doi: 10.1128/AAC.46.12.4038-4040.2002
Resende, J. A., Diniz, C. G., Silva, V. L., Otenio, M. H., Bonnafous, A., Arcuri, P. B., et al. (2014). Dynamics of antibiotic resistance genes and presence of putative pathogens during ambient temperature anaerobic digestion. J. Appl. Microbiol. 117, 1689–1699. doi: 10.1111/jam.12653
Rizzo, L., Manaia, C., Merlin, C., Schwartz, T., Dagot, C., Ploy, M. C., et al. (2013). Urban wastewater treatment plants as hotspots for antibiotic resistant bacteria and genes spread into the environment: a review. Sci. Total Environ. 447, 345–360. doi: 10.1016/j.scitotenv.2013.01.032
Roberts, M. (2015). Distribution of Tet Resistance Genes among Gram-Negative Bacteria. Available online at: http://faculty.washington.edu/marilynr/ (Accessed June 13, 2015).
Roberts, M. C. (1996). Tetracycline resistance determinants: mechanisms of action, regulation of expression, genetic mobility, and distribution. FEMS Microbiol. Rev. 19, 1–24. doi: 10.1111/j.1574-6976.1996.tb00251.x
Roberts, M. C. (2005). Update on acquired tetracycline resistance genes. FEMS Microbiol. Lett. 245, 195–203. doi: 10.1016/j.femsle.2005.02.034
Rossolini, G. M., D'Andrea, M. M., and Mugnaioli, C. (2008). The spread of CTX-M-type extended-spectrum beta-lactamases. Clin. Microbiol. Infect. 14, 33–41. doi: 10.1111/j.1469-0691.2007.01867.x
Schlüter, A., Szczepanowski, R., Puhler, A., and Top, E. M. (2007). Genomics of IncP-1 antibiotic resistance plasmids isolated from wastewater treatment plants provides evidence for a widely accessible drug resistance gene pool. FEMS Microbiol. Rev. 31, 449–477. doi: 10.1111/j.1574-6976.2007.00074.x
Stalder, T., Alrhmoun, M., Louvet, J. N., Casellas, M., Maftah, C., Carrion, C., et al. (2013). Dynamic assessment of the floc morphology, bacterial diversity, and integron content of an activated sludge reactor processing hospital effluent. Environ. Sci. Technol. 47, 7909–7917. doi: 10.1021/es4008646
Stalder, T., Barraud, O., Casellas, M., Dagot, C., and Ploy, M. C. (2012). Integron involvement in environmental spread of antibiotic resistance. Front. Microbiol. 3:119. doi: 10.3389/fmicb.2012.00119
Stoddard, S. F., Smith, B. J., Hein, R., Roller, B. R. K., and Schmidt, T. M. (2015). rrnDB: improved tools for interpreting rRNA gene abundance in bacteria and archaea and a new foundation for future development. Nucleic Acids Res. 43, D593–D598. doi: 10.1093/nar/gku1201
Storteboom, H., Arabi, M., Davis, J. G., Crimi, B., and Pruden, A. (2010). Tracking antibiotic resistance genes in the South Platte River Basin using molecular signatures of urban, agricultural, and pristine sources. Environ. Sci. Technol. 44, 7397–7404. doi: 10.1021/es101657s
Suzuki, M. T., Taylor, L. T., and DeLong, E. F. (2000). Quantitative analysis of small-subunit rRNA genes in mixed microbial populations via 5′-nuclease assays. Appl. Environ. Microbiol. 66, 4605–4614. doi: 10.1128/AEM.66.11.4605-4614.2000
Szczepanowski, R., Linke, B., Krahn, I., Gartemann, K. H., Gutzkow, T., Eichler, W., et al. (2009). Detection of 140 clinically relevant antibiotic-resistance genes in the plasmid metagenome of wastewater treatment plant bacteria showing reduced susceptibility to selected antibiotics. Microbiology 155, 2306–2319. doi: 10.1099/mic.0.028233-0
Wellington, E. M. H., Boxall, A. B. A., Cross, P., Feil, E. J., Gaze, W. H., Hawkey, P. M., et al. (2013). The role of the natural environment in the emergence of antibiotic resistance in Gram-negative bacteria. Lancet Infect. Dis. 13, 155–165. doi: 10.1016/S1473-3099(12)70317-1
Wilson, C. A., Murthy, S. M., Fang, Y., and Novak, J. T. (2008). The effect of temperature on the performance and stability of thermophilic anaerobic digestion. Water Sci. Technol. 57, 297–304. doi: 10.2166/wst.2008.027
Yang, Y., Li, B., Zou, S. C., Fang, H. H. P., and Zhang, T. (2014). Fate of antibiotic resistance genes in sewage treatment plant revealed by metagenomic approach. Water Res. 62, 97–106. doi: 10.1016/j.watres.2014.05.019
Zhang, T., Yang, Y., and Pruden, A. (2015). Effect of temperature on removal of antibiotic resistance genes by anaerobic digestion of activated sludge revealed by metagenomic approach. Appl. Microbiol. Biotechnol. 99, 7771–7779. doi: 10.1007/s00253-015-6688-9
Zhang, T., Zhang, X. X., and Ye, L. (2011). Plasmid metagenome reveals high levels of antibiotic resistance genes and mobile genetic elements in activated sludge. PLoS ONE 6:e26041. doi: 10.1371/journal.pone.0026041
Zhang, X. X., Zhang, T., Zhang, M., Fang, H. H. P., and Cheng, S. P. (2009). Characterization and quantification of class 1 integrons and associated gene cassettes in sewage treatment plants. Appl. Microbiol. Biotechnol. 82, 1169–1177. doi: 10.1007/s00253-009-1886-y
Zhang, Y. P., Snow, D. D., Parker, D., Zhou, Z., and Li, X. (2013). Intracellular and extracellular antimicrobial resistance genes in the sludge of livestock waste management structures. Environ. Sci. Technol. 47, 10206–10213. doi: 10.1021/es401964s
Keywords: mesophilic anaerobic digestion, thermophilic anaerobic digestion, antibiotic resistant bacteria, tetracycline, antibiotic resistance gene, horizontal gene transfer, biosolids
Citation: Miller JH, Novak JT, Knocke WR and Pruden A (2016) Survival of Antibiotic Resistant Bacteria and Horizontal Gene Transfer Control Antibiotic Resistance Gene Content in Anaerobic Digesters. Front. Microbiol. 7:263. doi: 10.3389/fmicb.2016.00263
Received: 26 December 2015; Accepted: 17 February 2016;
Published: 08 March 2016.
Edited by:
Charles W. Knapp, University of Strathclyde, UKReviewed by:
Jose Luis Balcazar, Catalan Institute for Water Research, SpainAndrew C. Singer, NERC Centre for Ecology & Hydrology, UK
Copyright © 2016 Miller, Novak, Knocke and Pruden. This is an open-access article distributed under the terms of the Creative Commons Attribution License (CC BY). The use, distribution or reproduction in other forums is permitted, provided the original author(s) or licensor are credited and that the original publication in this journal is cited, in accordance with accepted academic practice. No use, distribution or reproduction is permitted which does not comply with these terms.
*Correspondence: Amy Pruden, YXBydWRlbkB2dC5lZHU=