Bacterial Community Analysis of Drinking Water Biofilms in Southern Sweden

Next-generation sequencing of the V1–V2 and V3 variable regions of the 16S rRNA gene generated a total of 674,116 reads that described six distinct bacterial biofilm communities from both water meters and pipes. A high degree of reproducibility was demonstrated for the experimental and analytical work-flow by analyzing the communities present in parallel water meters, the rare occurrence of biological replicates within a working drinking water distribution system. The communities observed in water meters from households that did not complain about their drinking water were defined by sequences representing Proteobacteria (82–87%), with 22–40% of all sequences being classified as Sphingomonadaceae. However, a water meter biofilm community from a household with consumer reports of red water and flowing water containing elevated levels of iron and manganese had fewer sequences representing Proteobacteria (44%); only 0.6% of all sequences were classified as Sphingomonadaceae; and, in contrast to the other water meter communities, markedly more sequences represented Nitrospira and Pedomicrobium. The biofilm communities in pipes were distinct from those in water meters, and contained sequences that were identified as Mycobacterium, Nocardia, Desulfovibrio, and Sulfuricurvum. The approach employed in the present study resolved the bacterial diversity present in these biofilm communities as well as the differences that occurred in biofilms within a single distribution system, and suggests that next-generation sequencing of 16S rRNA amplicons can show changes in bacterial biofilm communities associated with different water qualities.

Biofilms are populations of microorganisms that are typically concentrated at a solid-liquid interface and surrounded by an extracellular polymeric substance matrix (13). The presence of extracellular polymeric substances within the biofilm protects bacteria by making them more resistant to chemicals such as disinfectants (10). The environment within a drinking water distribution system (DWDS) is oligotrophic and can contain disinfectants, with more than 95% of the bacterial biomass occurring as biofilms on the inner surface of the DWDS and less than 5% existing in the planktonic form (9). Biofilms in the distribution system constitute an ecosystem that can influence the esthetic quality of drinking water by altering taste, color, and odor, and also microbial water quality through the detachment of biomass into the bulk water (22). Bacterial biofilms have also been associated with technical problems within the DWDS such as corrosion (41). Although biofilms are known to have these impacts on drinking water, little is known about the mechanisms involved; therefore, a deeper understanding of the mechanisms by which the microbes in this human-built ecosystem participate in the delivery of drinking water to consumers need to be elucidated in more detail.
Less than 1% of bacteria in fresh and drinking water are currently culturable and bacteria in drinking water biofilms can also be present in a viable but non-culturable (VBNC) state (1,20,37,40). Therefore, culture-independent methods are preferable for providing a more complete picture of the microbial community; however, this type of analysis may not distinguish between dead or living cells (30). While methods using clone libraries, DGGE, and other DNA-based methods have contributed descriptions of the microbes present in drinking water biofilms (8,33,42), next-generation sequencing (NGS) is considered to provide the most detailed, high throughput, culture-independent method for the characterization of microbial communities. Previous studies that have examined bacterial communities present in water or biofilms of the DWDS have used the NGS of amplicons from water meter biofilms (16), clear well biofilms (44), faucet biofilms (27), and biofilms in a pilot-scale microfiltration plant that treats drinking water (21). NGS has also been used to examine the impact of changing hydraulic regimes on the bacterial biofilm community structure in an experimental distribution system (5) as well as the influence of chloramination and chlorination on planktonic bacterial communities in water samples (19). However, the reproducibility of amplicon NGS for real DWDS biofilms, the diversity present across biofilms from a single distribution system, and the feasibility of using water meters to investigate changes associated with the consumer perception of water quality have not yet been investigated.
We herein examined bacterial communities in DWDS biofilms using a deep 16S rRNA amplicon NGS analysis. To obtain a representative drinking water biofilm, samples from water meters were analyzed from a single existing distribution network in southern Sweden. The reproducibility of this approach was demonstrated by comparing biofilms from water meters installed in parallel and, thus, experiencing nearly identical hydrological environments. In addition, we showed that differences in the biofilm community composition in water meters and pipes as well as perceived water qualities within a single DWDS were resolvable.

Sampling
Six biofilm samples were collected from the DWDS of the city of Landskrona (Sweden) in March, April, and June, 2011 (Table 1). Water meter biofilms were sampled using sterile cotton transport swabs. Biofilm samples from the walls of the pipes were taken with a sterile cell spatula (TPP, Trasadingen, Switzerland) and the collected material was resuspended in approximately 5 mL of water from the sampling site. All samples were transported to the laboratory in a cooling box within 8 h after sampling and then stored at -20°C until further analyses. Water samples for water quality testing were taken from households during the sampling of water meter biofilms and the results obtained were reported together with general water quality data representative for drinking water in the city of Landskrona (Sweden) (

Generation of amplicons
DNA was extracted from cotton swabs or 200 µL resuspended biofilm material using the Fast DNA Spin Kit for Soil (MP Biomedicals) and a bead beater. DNA from two cotton swabs was extracted for each sample, pooled together, and diluted 10-fold before PCR amplification. DNA was also extracted from empty cotton swabs and MilliQ water as negative controls for PCR. PCR amplification of a specific bacterial 16S rRNA region was performed using the primers 27F (5' GS FLX Titanium adapter A -TCAG -MID -AGAGTTTGATCCTGGCTCAG 3') and 534R (5' GS FLX Titanium adapter B -TCAG -MID -ATTACCGCGGCTGCTGGC 3') (16) with adapter A representing the forward 454 sequencing primer, adapter B representing the 454 reverse primer, and a 10-bp long sample-specific barcode (MID). Barcodes recommended by Roche were used with the following sequences: ACGAGTGCGT (MID1 for P1), ACGCTCGACA (MID2 for P2), AGACGCACTC (MID3 for WM 4), AGCACTGTAG (MID4 for WM 3), ATCAGACACG (MID5 for WM 1), and ATATCGCGAG (MID6 for WM 2). PCR reactions were carried out in a C1000 thermal cycler (Bio-Rad) and contained: 1 × PicoMaxx Reaction buffer, 2 mM MgCl 2 , 0.2 mM of each dNTP, 0.8 µM of each forward and reverse primer, 1.5 U PicoMaxx polymerase, and 5 µL of template DNA (diluted 10-fold) in a total volume of 30 µL. The cycling parameters were: 5 min at 95°C, followed by 30 cycles of 95°C for 1 min, 55°C for 1 min, 72°C for 1 min, and a final 72°C held for 5 min. Two to three PCR reactions were carried out for each biofilm sample, and pooled together for amplicon purification. The FAST DNA Spin Kit for Soil has been proposed as the method of choice for DWDS DNA extraction, generating representative community information and reproducibility, while PicoMaxx polymerase efficiently amplifies low amounts of DNA in the presence of PCR inhibitors (15,18). A high concentration of primers was used to outcompete partially extended primers and reduce the formation of chimeras (36).

Amplicon library preparation
Pooled amplicons were purified using the E.Z.N.A ® Cycle Pure Kit (OMEGA, Bio-tek) and Cycle-Pure Spin Protocol according to the manufacturer's instructions. Sequencing was conducted at the Lund University Sequencing Facility, Sweden. Pooled amplicons were reduced for short fragments by using Agencourt AMPure XP (Beckman Coulter) and inspected using a DNA 1000 kit on a 2100 Bioanalyzer (Agilent). Amplicons were quantified using the Quant-iT dsDNA assay kit (Invitrogen) and Quantifluor fluorometer (Promega), and pools were diluted to obtain a total of 1×10 7 copies µL -1 . Titration and library production (aiming at 10-15% enrichment) were performed using emulsion PCR and the Lib-A kit (Roche). DNA-positive beads were enriched, counted on an Innovatis CASY particle counter (Roche), processed using the XLR70 sequencing kit (Roche), and loaded onto a picotiter plate for pyrosequencing on a 454 Life Sciences Genome Sequencer FLX machine (Roche). DNA sequences were archived at NCBI SRA under the accession number SRP039011.

Data analysis
Amplicons were sequenced from both directions, with reads from forward (V1-V2 region) and reverse (V3 region) directions being treated separately during data analysis following the cleaning step (Supplemental Fig. S1). Reads were sorted by a barcode using sfffile (SFF Tools, Roche). The barcode and TCAG-tags were also removed using sfffile. Reads were quality filtered using PrinSeq lite (v 0.19.3) (34) and custom Perl scripts and discarded if they were shorter than 220 bp, longer than 650 bp, contained ambiguous base pairs, or had a mean quality score below 25. Reads were trimmed after 350 bp or if the mean quality score within a 50 bp sliding window with a step size of 1 was less than 35. Reads with a perfect match to the primer in the 5' region (27F or 534R) were kept and the sequence information corresponding to the primer region was removed. Reads from the reverse direction were converted to their reverse complement using custom Perl scripts. Chimera checking was done using Uchime (7) in the de novo mode after de-replication as implemented in Usearch (v 5.2.32) (6). Reads detected as chimeras were removed from the dataset. In order to avoid bias, sequences were randomly subsampled without replacement to the smallest sample size using the Perl script daisychopper.pl (http://www. genomics.ceh.ac.uk/GeneSwytch/Tools.html v0.6) (11). The subsampled sequences were classified using the command line version of the RDP classifier (v. 2.5) (43) and clustered using CROP (v133) with the option -s corresponding to a 97% sequence identity (14). The parameters were 3176 for -b and 480 for -z for both forward and reverse reads. CROP was run on the Lunarc supercomputer at Lund University. Only clusters with at least 20 sequences in one of the six samples were kept to construct a phylogenetic tree. Metaxa (v 1.1) was applied to detect sequences of chloroplasts, mitochondria, archaea, and eukaryotes (2). Sequences were aligned using Greengenes (4) (greengenes.lbl.gov), and a phylogenetic tree was constructed using RAxML (38) and displayed in iTOL (24). OTUs detected by Metaxa as being chloroplasts or having an uncertain origin, or OTUs that did not align to the Greengenes reference dataset were removed before construction of the phylogenetic tree (see Supplemental Fig. S2).

16S rRNA gene amplicon NGS of DWDS biofilms
Six biofilm samples from a single DWDS were selected for a detailed community analysis using NGS of the 16S rRNA gene. The aim was to permit comparisons of both dominant and rare members of the communities to determine whether the community changed with location as well as the number of sequences required to resolve these differences between samples.
Sequences obtained from the forward reads encompassed the V1-V2 region of the 16S rRNA gene while reverse reads corresponded to the V3 region. A total of 674,116 reads describing the six bacterial biofilm communities were initially obtained; 174,817 of these reads did not meet the quality requirements and were removed, and random subsampling selected 52,932 sequences (26,466 for each read direction) to represent each biofilm community (Table 3). Sequences used for analyses ranged in length from 200-332 bp, with an average length of 312 bp after trimming and cleaning. Sequences describing either the V1-V2 region or V3 region were classified using the RDP classifier at a confidence level of 80%. Classification of the V1-V2 and V3 regions showed highly similar trends with respect to the community composition for each biofilm sample at the phylum (Fig. 1) and class (Fig. 2) level.
Sequences were clustered into OTUs (phylotypes), applying a threshold corresponding to 97% identity. OTUs relevant for comparisons of the distinct biofilm bacterial communities were restricted to those containing 20 or more sequences from any one of the six biofilm samples in order to avoid including sequences containing errors introduced during sequencing or PCR amplification (17). The removal of rare sequences reduced the number of OTUs from 2,383 to 308. The number of OTUs representing each of the six biofilm communities ranged from 126 to 227 (Table 3, V1-V2 region) with 57 of these 308 OTUs being present in all the biofilm communities examined. Since comparisons of information obtained from the V1-V2 and V3 regions by both RDP classification ( Fig. 1 and Fig. 2) and OTU frequencies (Fig. 3, 4, Table 4 and 5) gave similar results, the V1-V2 region was chosen to facilitate comparisons between the different biofilm communities.
Assessment of reproducibility using biofilm communities from parallel water meters Bacterial biofilm communities in water meters (WM) installed in parallel within the DWDS were physically present on distinct surfaces of two water meters (WM 1 and WM 2), and had developed for four years within an apartment building that had experienced identical temperatures, seasons, water flow, and source water (Supplemental Fig. S3). The analysis of these two communities was used to examine the reproducibility of the established high resolution sequencing work-flow for determining community compositions, OTU frequencies, and phylotypes. WM 1 and WM 2 were dominated at the phylum level by Proteobacteria (82% for WM 1; 87% for WM 2), and unclassified Bacteria (11% for WM 1; 8% for WM 2, Fig. 1). A total of 185 OTUs were identified in WM 1 and 177 OTUs in WM 2, with the two communities sharing 163 OTUs and 75% of the sequences (Fig. 3). A heatmap illustrating the 50 most abundant OTUs showed highly similar profiles of OTU frequencies for both water meters (Fig. 4).
To determine whether the bacterial biofilm community changed within a single DWDS or if the water meter biofilms were similar throughout the same DWDS, biofilms were sampled from a third water meter (WM 3) connected to the same distribution system a few kilometers away from the WM 1 and 2 sampling site.    Table 3. All OTUs and sequences were considered in the sequence-based comparison (right panel). Each sample contained 26,466 sequences. The number of shared sequences between samples was determined for each OTU and then summed to give the total number of all shared sequences for the samples being compared.
WM 3 was also dominated by Proteobacteria and gave a similar overall picture at the phylum and class levels as WM 1 and WM 2 ( Fig. 1 and Fig. 2). Sequences from WM 3 were classified into the 20 most abundant OTUs in largely the same proportions as those classified for WM 1 and WM 2 ( Table  4). These included OTUs of Sphingomonadaceae (40%), Hyphomicrobiaceae (20%), and unclassified Proteobacteria (13%). The diversity of WM 3 was represented by slightly fewer OTUs (a total of 129) than WM 1 and WM 2 (185 and 177, respectively) ( Table 3). WM 3 shared 114 OTUs and 42% of the sequences with WM 1, and 113 OTUs and 60% of the sequences with WM 2 (Fig. 3).

A bacterial biofilm from an area with unacceptable water quality
A biofilm from a fourth water meter within the same DWDS was sampled from a location in which problems with water quality had been reported by the consumer in order to determine whether changes within the bacterial biofilm community associated with changes in water quality could be resolved.
Differences were observed at the phylum level between WM 4 and WM 1-3. Proteobacteria were less abundant than in the other water meters (44% in WM 4 and 82-87% in WM 1-3). However, the composition of classes within the Proteobacteria remained the same across all WMs with  Alphaproteobacteria as the most abundant class (Fig. 2). Planctomycetes (4%), Acidobacteria (7%), and Nitrospira (11%) were present in WM 4 and virtually absent in any of the other samples. The amount of unclassified bacteria in WM 4 was the highest at 30%, while these amounts were only 2-13% in the other five samples. Within the 20 most abundant OTUs, only 1% of the WM 4 sequences belonged to the OTU classified as family Sphingomonadaceae.
Certain OTUs contained a large number of sequences from WM 4, but were not represented in other WMs, including sequences classified as genus Nitrospira (11%) and genus Pedomicrobium (7%) for WM 4. WM 4 contained 227 OTUs, the highest number of OTUs found in any of the six biofilm samples. WM 4 and WM 3 shared 102 OTUs, similar to the amount of shared OTUs observed between other samples (Fig. 3); however, only 8% of the sequences were shared. Differences in the abundance of the sequences with the OTUs obtained from WM 4 differentiated this bacterial biofilm community from those of WM 1-3: the heatmap profile of OTU frequency (Fig. 4) showed that the distribution of sequences across OTUs was distinct for WM 4.

Bacterial community composition in DWDS pipes
A biofilm was sampled from a pipe (P1) to compare the pipe bacterial biofilm community adjacent to the biofilm communities established on water meters. A second pipe (P2) was selected as a biofilm community from the same DWDS, but with a number of distinct characteristics such as the age of the biofilm (Table 1). An analysis at the phylum level ( Fig. 1) showed that P1 was dominated by Proteobacteria (58%) and Actinobacteria (39%), with other phyla accounted for less than 3% of the sequences.
P1 contained 126 OTUs, the fewest OTUs found in any of the samples examined, sharing 110 OTUs with WM 1 and 106 OTUs with WM 2 (Fig. 3). As observed with WM 4, despite the number of shared OTUs between samples, P1 shared fewer sequences with WM 1 (21%) and WM 2 (23%).
At the phylum level, sequences obtained from P2 consisted of 86% Proteobacteria and 5% unclassified Bacteria with other phyla accounting for less than 3%, as observed for P1. Within Proteobacteria, both pipes consisted of sequences more widely distributed across the different classes, and were not predominated by Alphaproteobacteria as observed for WM 1-3 and WM 4 (Fig. 2). A small overlap in the community structure was observed between P1 and P2. OTU frequencies gave a heatmap profile of P2 that was distinct from all other samples, with the highest OTU frequencies appearing in OTUs that were not predominant in any other sample examined; for example Desulfovibrio (9%), and Sulfuricurvum (6%) (Fig. 4), and, although a number of the OTUs themselves were shared, only 21% of the sequences were shared between P1 and P2 (Fig. 3).

Discussion
The bacterial communities present in six samples from a single DWDS system in Sweden were analyzed using amplicon NGS of the V1-V2 and V3 regions of the 16S rRNA gene. Sampling sites were chosen to test the resolution and limits of the experimental and analytical protocols, and to determine whether the described work-flow was capable of resolving community changes associated with small variations in a DWDS ecosystem.
Although the most relevant analysis of drinking water biofilms is an examination of those within established drinking water delivery networks, one difficulty associated with working in these systems is obtaining biological replicates to validate the experimental approach. In this study, bacterial biofilm communities of parallel installed water meters (WM 1, WM 2) allowed an approach to be developed and tested for a high resolution community analysis through NGS that included controls for both the experimental approach, by comparing results between WM 1 and WM 2, as well as the influence of changes in the DWDS on the community, by comparing additional drinking water biofilms.
Biofilms from virtually identical locations and sampling regimes associated with WM 1 and WM 2 showed highly similar communities when described by any of the NGS analyses in this study. This degree of similarity between two descriptions of communities has not been reported in previous studies that used NGS to examine the bacterial communities of drinking water biofilms, and may reflect the difficulty in obtaining true biological replicates in working DWDSs. Even small variations in the ecology of the drinking water biofilm can affect the community composition. Hong et al. (16) observed numerous differences in communities associated with two water meters that had experienced stable turbidity, pH, and chlorine levels, but differed in the origin of the water meter (two separate households) and the time of year they were sampled (October and December). Douterelo et al. (5) examined biofilm communities within a model DWDS, including NGS of material assumed to be biological replicates; however, even samples retrieved from this highly homogenous model system produced biofilm communities that showed a high variability in biological diversities across three biological replicates. The diversity was suggested to have been linked to the short time (28 d) over which the biofilms were grown, and Martiny et al. (29) showed that biofilms in a model drinking water system followed a successional formation that only culminated in a stable population after three years. Thus, the high similarity between WM 1 and WM 2 is a reflection of the nearly identical physical and temporal parameters that nurtured the ecology of these two biofilms. This result strongly suggests that the differences observed in the other WM communities arose from ecological changes and not from experimental or analytical artefacts and, in addition to physical parameters defining the ecosystem, the time over which this biofilm developed also contributed to the consistency of the observed community composition.
The results obtained for WM 1 and WM 2 suggest that differences in the WM 3 composition were related to changes in the environment of WM3; small differences in the community, OTU, and phylotype comparisons may be due to changes in the geographical location of WM 3 and/or water consumption associated with this biofilm community relative to WM 1 and WM 2. The biofilms in WM 1 and WM 2 were obtained from a building with high water consumption (436 and 527 m 3 over six months, respectively), whereas that in WM 3 was obtained from a water meter within a family house that had a lower water consumption of 49 m 3 over six months. The communities in WM 4, and P1 and P2 pipe biofilms, may have diverged from those of WM 1-3 to the degree that the surrounding environment of the biofilm differed. Since the environment of WM 4 was the most similar to that of WM 3 (Table 1), differences in this community may be explained by its unique location within the DWDS, and/or the distinct water quality profile associated with this sample. The composition of biofilms was different in pipe biofilm communities and those in water meters, while similar OTUs were present in both types of samples, but only a low percentage of sequences were shared (Fig. 3). The hydrological characteristics (i.e. pipe diameter), geographical location (including temperature), sampling season, microbial corrosion, and age of the biofilm differed between P1 and P2, which made it difficult to define any relationship between community composition and any DWDS or sampling parameters.
In addition, sampling of pipe biofilms within a working DWDS is often determined by the water company's activities, which further limits study design. The location of the water meter biofilm at the boundary between the drinking water provider and consumer often represents a change in responsibility for water quality and, together with the results presented here, support and strengthen the application of sampling water meters for biofilm communities in contact with drinking water. In contrast, water meters contain structures and surfaces for the establishment of biofilms that are the same at each sampling location; therefore, the possibility exists for biological replicates within a DWDS if parallel water meters have been installed in some buildings, and installation and removal is simple and monitored so the length of time for the biofilm to have become established is known. Hong et al. (16) also proposed that biofilms obtained from water meters were suitable for studying the microbial ecology of DWDS due to the ease of sampling. With uniform physical structures and the possibility for more standardized sampling, comparisons of WM communities can more directly be related to variables such as water quality and/or water usage.
Large numbers of sequences that clustered into OTUs described as Sphingomonadaceae were found in the water meter samples WM 1-3, with a reduced number of sequences being detected for this group in WM 4. Sphingomonadaceae have previously been detected in drinking water systems (16,44) and have been related to drinking water quality because they may be responsible for initial biofilm formation (3) and are very resistant to chlorine (39). These phenotypes may promote bacterial growth in the distribution system and, thus, influence drinking water quality. The WM 4 community had a reduced number of sequences that were classified as Sphingomonadaceae, and a community composition distinct from the other water meters in this study. This was also observed at phylum level, with Proteobacteria, the most abundant phylum in the drinking water biofilms analyzed in this study and others (16,25,33,44), being markedly reduced in WM 4. A decrease in bacterial biofilm diversity has been associated with a loss of multifunctionality (31) and the larger number of OTUs observed at WM 4 may reflect a more diverse substrate or more active biofilm using the wider spectrum of nutrients present in less-than-ideal drinking water.
Since water consumption was similar between WM 3 and 4 (49 m 3 in six months for WM 3 and 53 m 3 in 6 months for WM 4), other factors may account for the differences observed between these biofilm communities.
Sequences related to Nitrospira were more abundant in WM 4 than in WM 1-3. Ling and Liu (26) observed a community shift to Nitrospirae in unchloraminated biofilms, suggesting the sensitivity of Nitrospirae to the disinfection treatment, and Nitrospira was previously detected in a model DWDS using unchlorinated groundwater (29). Even though chlorination has been used for disinfection in the DWDS examined in this study, water samples characterizing flowing water moving past the WM 4 biofilm had a lower total chlorine concentration (0.05 mg L -1 Cl 2 ) than those for the other WM communities (WM 1, WM 2: 0.13 mg L -1 Cl 2 ; WM 3: 0.14 mg L -1 Cl 2 ). Lower chlorine levels may be related to the report of red water for WM 4, as an increase in biofilm activity (due to reduced exposure to a disinfectant) has been associated with an increase in the deposition of iron and manganese into biofilms (12). Cell death within the biofilms or disruption due to hydraulic changes may release deposited iron and manganese, resulting in red water and the elevated levels of iron and manganese previously observed during discolored water events (35). Li et al. (25) reported changes in the bacterial community associated with the occurrence of red water and observed a higher percentage of the iron-oxidizing bacteria Gallionella together with the extensive precipitation of iron oxides in water samples. Although Gallionella was not detected in the present study, Pedomicrobium was identified in WM 4, the only community that was exposed to flowing water containing detectable iron and manganese concentrations (1.5 mg L -1 Fe and 0.04 mg L -1 Mn). The presence of these metals within the water may support the growth of Pedomicrobium, which deposits oxidized metals on its cell surface, resulting in the accumulation of metal oxides in biofilms (23,32).

Conclusion
This study has established a work-flow that has the ability to resolve biofilm communities in sufficient detail to permit their composition to be related to the ecology of real DWDS biofilms; therefore, a definitive relationship between bacterial community compositions may be established by using this approach with a large number of biofilm samples representing diverse properties and qualities of both drinking water and its distribution systems. The high reproducibility observed between the two parallel installed water meters and other water meters from the same city suggests that water meters are an appropriate sampling site if the aim is to compare different locations within a DWDS. This study demonstrated that differences between drinking water biofilms were observable at the phylum level, which indicated that sequencing of the V1-V2 region of the 16S rRNA gene may provide sufficient information regarding bacterial community compositions for high throughput analyses and comparisons. Lundin et al. (28) suggested that 5,000 sequences allowed trends in alpha diversity to be estimated; hence, using fewer sequences from a single 16S region and biofilm from easily accessible water meters will facilitate the analysis of many bacterial biofilm communities associated with differing water qualities. The results of the present study support this experimental and analytical approach as a strategy for compiling an accurate and complete knowledge of the ecology of DWDS biofilms and their role in drinking water delivery.