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Water samples of the Drinking Water Supply System (DWSS) of the city of Braunschweig were analysed for its Legionella species composition using genus-specific PCR amplicons and single-strand conformation polymorphism (SSCP) fingerprint analyses based on 16S rRNA genes. These analyses comprised the whole supply chain including raw water, treatment process and large-scale storage, and a seasonal study of finished drinking water sampled monthly from cold and hot tap water. Treatment of raw water had a major impact on Legionella species by reducing their diversity and abundances. The Legionella species composition of the tap water was highly distinct from that of both source waters. In cold water, 8–14 different phylotypes of Legionella (PTLs) were observed per sample with relative abundances ranging from >1% to 53%. In hot water, L. pneumophila was present during all seasons at high relative abundances (8–40%) accompanied by 5–14 other PTLs of which 6 PTLs were in common with cold water. This thermophilic Legionella community, including L. pneumophila, was able to grow in the hot water above 50°C. Such thermophilic Legionella populations are of general relevance for drinking water management and public health, but also for the ecology and evolution of the genus Legionella.
The genus Legionella comprises currently 59 species of which about half have been demonstrated to be pathogenic to humans, and the majority is considered as facultative pathogenic (Mercante and Winchell, 2015). The most well-known and best-studied Legionella species is L. pneumophila because it is the aetiological agent of legionellosis (primarily lung infections) in >90% of the cases -in most countries where appropriate surveillance is in place (Bartram et al., 2007; European Centre for Disease Prevention and Control, 2015). Non-pneumophila Legionella species account usually for <10% of human infections, especially L. micdadei, L. bozmanii, L. longbeachae, L. dumoffii and L. feeleii are isolated repeatedly from hospitalized patients whereas L. anisa, L. wadsworthii and L. cincinnatiensis are only rarely found (Yu et al., 2002; Beauté et al., 2013; European Centre for Disease Prevention and Control, 2015). A special case is L. longbeachae that accounts for about 30% of the human Legionella infections in Australia (Fields et al., 2002; Whiley and Bentham, 2011). The genus Legionella has the highest human health relevance for water-based bacterial infections with respect to fatality in the developed countries (Phin et al., 2014).
In Europe, local legionellosis outbreaks due to aerosols distributed by cooling towers and spas regularly affect hundreds of people despite strict control and surveillance measures. Most cases, however, are caused by sporadic infections and contaminated water systems still pose the greatest threat to public health (European Centre for Disease Prevention and Control, 2015). Despite a substantial amount of research on the ecology, the physiology and the molecular virulence mechanisms of Legionella since its discovery annual incidence rates remained on a high level (Fields et al., 2002; Phin et al., 2014; European Centre for Disease Prevention and Control, 2015).
Most Legionella species are of aquatic origin including L. pneumophila; a few are also isolated from non-aquatic habitats such as potting soil and compost (especially L. longbeachae) (Fields et al., 2002; Borella et al., 2005a; Casati et al., 2010; Lück et al., 2010; Whiley and Bentham, 2011; Travis et al., 2012; Currie et al., 2014). Many Legionella species are considered well adapted to low-nutrient conditions in water, and therefore pre-adapted to conditions in drinking water (Vervaeren et al., 2006). Best studied are the environmental reservoirs of L. pneumophila, which has been found in natural freshwater environments such as lakes, streams and Drinking Water Supply Systems (DWSS) (Fields, 1996). In DWSS, L. pneumophila survives planktonically, grows in biofilms and infects and replicates within protozoa (Steinert et al., 2002; Molmeret et al., 2005; Declerck et al., 2007b; Steinert et al., 2007). These bacteria can survive in moist places for a long time at relatively high temperatures and in the presence of disinfectants such as chlorine (Dupuy et al., 2011).
Temperature is an important factor for the abundance and growth of Legionella in natural and man-made aquatic systems. Legionella are mesophilic with a temperature range for growth ranging from 12°C to 42°C and an optimum from 25°C to 40°C (Ohno et al., 2003). This is the reason why warm water systems (showers, cooling towers and air conditioners) were often shown to be of special health relevance, and heating above 50°C is highly recommended to decrease the risk of legionellosis (Stout et al., 1986). Temperature might also be a key factor for the annual summer peak of Legionella cases observed in Europe (Joseph et al., 2010; Beauté et al., 2013). On the average, in late winter (February and March) a minimum in the number of cases is observed which is followed by a 3- to 4-fold increase in summer with a maximum in August. Due to this seasonality of Legionella infections, it might be worthwhile studying seasonal effects on their abundances in drinking water to understand their environmental control factors. Seasonal variations of Legionella spp. communities have already been detected in natural waters and reservoirs, but these studies did not include the connected DWSS (Parthuisot et al., 2010; Kao et al., 2014).
Next to temperature, the abundances of Legionella species in aquatic ecosystems are controlled by a variety of factors such as available nutrients, grazing by protozoa and eventually by lysis of bacteriophages in a regulatory circuit called microbial loop (Lammertyn et al., 2007; Pomeroy et al., 2007; Abdel-Nour et al., 2013). In addition to these classical ecological parameters, concentrations of disinfectants have an important role in many DWSS as essential abiotic regulators. In man-made freshwater supply systems, treatment procedures further remove particles from the source water as well as components of the original food web and the subsequent preparation of hot water applies substantial temperature stress on the remaining microbiota. Some of these processes were shown to have a major impact on the bacterial community and have not yet been assessed for Legionella in surface water-derived drinking water (Eichler et al., 2006; Henne et al., 2013). Eichler et al. (2006) demonstrated for a DWSS that the overall bacterial community of the surface water (deep water from two reservoirs) changed very little due to processing by sand filtration and flocculation. However, chlorination had a major impact on the species composition and increased the abundance of presumably nitrifying taxa. The present bacterial community in the finished drinking water, on the other hand, was still composed to a large extent of taxa derived from the two reservoirs while only the active fraction of the community was substantially altered. In contrast, an almost complete change of the bacterial community was observed during hot water preparation by heating cold drinking water to about 63°C (Henne et al., 2013). The majority of the cold water bacteria decayed during heating with their nutrients being used by a rapidly growing hot water community reaching finally cell numbers of about 80% of the cold water community. Most bacterial members of the hot water community were phylogenetically closely affiliated with thermophilic species.
Currently, there is a very restricted set of studies on Legionella species diversity in DWSSs; most studies have concentrated on L. pneumophila. Wullings and van der Kooij (2006) provided a first molecular survey on Legionella species occurring in surface- and groundwater-based source waters and the respective finished drinking water in the Netherlands, showing that surface waters tend to lead to a higher Legionella load in drinking water. In addition, Wullings et al. (2011) described the Legionella diversity of two groundwater-based DWSS, showing that Legionella abundance and diversity is influenced by the dissolved organic carbon in source and drinking water. So far, there is neither a study following the seasonal diversity and dynamics of the genus Legionella from source water via cold to the hot drinking water nor a study that sees the Legionella dynamics in the frame of the overall bacterial community.
Our study aims to understand the composition and dynamics of Legionella communities in drinking water as a result of the typical treatments for drinking water processing such as raw water flocculation, sand filtration, chlorination, storage and hot water preparation. Based on our previous studies and the overall understanding of the total bacterial community of a DWSS (Eichler et al., 2006; Kahlisch et al., 2012; Henne et al., 2013), we will provide detailed insights into the community ecology of a highly health relevant genus, that is, Legionella, its changes and their triggering factors. In our DWSS, the following approach was pursued to accomplish our objectives: (i) genus-specific single-strand conformation polymorphism (SSCP) fingerprints were analysed to illustrate changes in the Legionella community structure along the drinking water production line and during a seasonal cycle of the finished drinking water before and after the heating process; (ii) single phylotypes were identified by sequencing of major bands to assess phylogenetic community compositions; (iii) community structures and compositions were compared with respect to the impact of drinking water processing, hot water production and season; (iv) the Legionella community and its dynamics were compared with the total bacterial community; (v) the contribution of the genus Legionella to the total bacterial community in terms of cell numbers was quantified by real-time PCR; and (vi) responses to water temperature of the whole Legionella community and abundant phylotypes were evaluated. To this end, we approached a better understanding of the long-term community ecology of the genus Legionella that is urgently needed for freshwater management and public health prevention measures.
Cold drinking water was sampled monthly from May 2008 to October 2009. It was taken from the tap of laboratory D0.04 on the campus of the Helmholtz Centre for Infection Research (HZI), Braunschweig, Germany, with 5-min flushing to prevent stagnant water to be sampled. In former studies, it was shown that the HZI campus drinking water is representative for the whole city area of Braunschweig with respect to physicochemical parameters and the bacterial community (Eichler et al., 2006; Henne et al., 2012).
Hot drinking water was sampled monthly from September 2008 to November 2009. It was taken from a shower next to lab D0.04 after several minutes flushing. The hot drinking water was made from the cold drinking water on the HZI campus by heating it up to 63°C (range: 60–63°C) in two 600-litre heating vessels. The cold drinking water was heated in the heating vessels together with the hot water of the circular systems at variable mixing ratios from about 1:1 to 1:10 (cold to hot water) during work hours, that is, our sampling time. More details about the cold and hot water supply system are given elsewhere (Eichler et al., 2006; Henne et al., 2013).
The drinking water originates from two surface water reservoirs (Grane reservoir, oligotrophic water, average dissolved organic carbon 2.2mg C l−1, 51° 45' 44” N, 10° 22' 38” E; Ecker reservoir, dystrophic water, average dissolved organic carbon 6.2mg C l−1, 51° 50' 27” N, 10° 34' 45” E) situated in the Harz Mountains 40 km south of Braunschweig. Processing of the drinking water by the local supplier Harzwasserwerke GmbH included flocculation/coagulation, sand filtration and chlorination (0.2–0.7mg chlorine l−1). At both reservoirs, the obtained raw water is processed similarly (sampling sites G=Grane and E=Ecker reservoir, samples for raw water are called GR1 and ER1, processed raw water is called GR2 and ER2, respectively). After treatment of the raw water by physical and chemical means, pipe systems lead from both reservoirs to the Lewerberg (Lb) storage container where both waters are mixed. This mixed water consisted of about 77% water from the Grane reservoir and 23% water from the Ecker reservoir. From the Lb container, the mixed water is transported to the Lindenberg (Li) storage container, directly located at the southern outskirts of Braunschweig, to which the local drinking water supply net is connected, including the sampled tap water source at the institute. The finished drinking water had an average dissolved organic carbon content of 1.6mg C l−1, with a maximum of 2.7mg C l−1 in early June. Samples along the water processing line from source water to the tap were collected on 3 May 2004. More details on the respective DWSS and sampling are given elsewhere (Eichler et al., 2006).
Drinking water microorganisms from cold and hot drinking water were sampled by filtration according to Eichler et al. (2006). In brief, 5litres of drinking water were filtered through a filter sandwich consisting of a 0.2-μm pore size polycarbonate filter (90mm diameter; Nucleopore; Whatman, Maidstone, UK) with a precombusted glass fibre filter on top (90mm diameter; GF/F; Whatman). Biomass harvested on filter sandwiches was stored at −70°C until further analysis.
For total bacterial cell counts, formaldehyde-fixed samples (2% final concentration) of drinking water were stained with Sybr Green I dye (1:10000 final dilution; Molecular Probes, Invitrogen, Carlsbad, CA, USA) and analysed directly by epifluorescence microscopy or stored frozen (−20°C) until examination as described in more detail by Henne et al. (2013).
For extraction of DNA from the filter sandwiches, a modified DNeasy protocol (Qiagen, Hilden, Germany) was used as described in detail by Henne et al. (2013). Quantification of DNA was carried out using Picogreen (dsDNA quantification, Molecular Probes; Invitrogen) according to the manufacturer.
For the SSCP fingerprints, a Legionella genus-specific PCR was performed using the biotinylated primer pair Lgsp17Fb (5′-bio-GGCCTACCAAGGCGACGATCG-3′) and Lgsp28R (5′-CACCGGAAATTCCACTACCCTCTC-3′) targeting the 16S rRNA gene (Kahlisch et al., 2010). For L. pneumophila, the amplicon size is 421bp spanning the V2 and V3 regions of the 16S rRNA (positions 264–661 E. coli numbering). Each amplification was carried out using 0.2–2.0ng of DNA template in a final volume of 50μl under the following conditions: Initial denaturation was at 95°C for 15min; followed by 35 cycles of denaturation at 95°C for 30s, annealing at 66.5°C for 30s, elongation at 72°C for 30s and final elongation for 10min at 72°C. Amplification was achieved using HotStarTaq DNA polymerase at 1Uμl−1, 2mm dNTPs, 2mm MgCl2 (all from Qiagen) and primers at a final concentration of 0.2μm (Eurofins MWG, Ebersberg, Germany) in the reaction buffer provided by the manufacturer of the DNA polymerase.
For the preparation of single-stranded DNA and the SSCP electrophoresis, the protocol described by Henne et al. (2013) was applied. After electrophoresis, the gel was silver stained according to Bassam et al. (1991). Dried SSCP gels were digitized using an Epson Expression 1600 Pro scanner (Epson, Long Beach, CA, USA). Sequence information of individual bands was obtained following the protocol of Eichler et al. (2006). The partial 16S rRNA gene sequences obtained from the genus-specific fingerprints are accessible under the GenBank/EMBL/DDBJ accession numbers KP822824 to KP822921 and KP863802 to KP863862. Individual accession numbers of representative sequences are listed in Supplementary Tables S1 and S2.
Forward and reverse sequences obtained from each excised band were assembled to contigs, analysed and manually checked using the Sequencher software (v. 5.2, Gene Codes Cooperation, Ann Arbor, MI, USA). Primer sequences were trimmed; resulting in partial 16S rRNA gene sequences of 376 bp. Fragments were checked for chimeras with the DECIPHER web tool (Wright et al., 2012) and pooled to clusters using the Sequencher's assembling tool for dirty data while applying a 99% sequence similarity threshold in order to group highly similar sequences while still discriminating between well-described species. Consensus sequences of each cluster were designated ‘phylotype of Legionella' (PTL-01 to -35) and ‘phylotype of reservoirs' (PTR-01 to -42), respectively. Phylogenetic identification of PTL and PTR consensus sequences was obtained by comparison with a curated database of type strain isolates using the Seqmatch function of the Ribosomal Database Project (RDP, accessed January 2015) (Cole et al., 2014). RDP Seqmatch results and similarity scores are listed in Supplementary Table S1 (PTRs) and Supplementary Table S2 (PTLs).
Digitized images of dried SSCP gels were analysed with the GelCompare II software (Applied Maths, Kortrijk, Belgium), bands were extracted applying appropriate settings (2.0% minimum profiling, 0.0% ‘grey zone', 0.5% minimum area and shoulder sensitivity=0) and edited manually (Supplementary Figure S3). Relative abundance measures for each band were obtained and assigned to its respective 16S rRNA gene sequence. Similarity matrices and Pearson's correlation coefficients of Legionella community fingerprints were calculated and subsequently, cluster analyses were performed by Neighbor-Joining algorithm.
Phylotype sequences were aligned with reference sequences of all 62 described Legionella type species (including subspecies) listed by the DSMZ (http://www.dsmz.de/bacterial-diversity/prokaryotic-nomenclature-up-to-date, last accessed: December 2014) using the RDP alignment tool. In case sequences of type strains had numerous ambiguous positions, additional high-quality sequences were searched in and extracted from the NCBI database and added to complement the alignment, for example, for L. hackeliae and L. spiritensis. The alignment was then further analysed in MEGA (version 6) (Tamura et al., 2013). Phylogenetic comparison was conducted calculating a Neighbor-Joining tree of 1000 bootstrap replicates using the Kimura 2-parameter model with a discrete Gamma distribution (shape parameter=5) and to allow for invariant sites (46.8%).
Species richness, evenness and abundance-weighted comparisons and other statistical analyses were conducted in R (v. 3.1.2, ‘Pumpkin Helmet') within the package Picante (v. 1.6–2) (Kembel et al., 2010). To compare Legionella community structures phylogenetically, Bray-Curtis distances among all samples were calculated to take phylotype composition and abundances into account. Samples were then hierarchically clustered using UPGMA in order to visualize Bray-Curtis dissimilarity and reveal seasonal clustering and differentiation, respectively. Mean pairwise distance (mpd) and mean nearest taxon distance (mntd) were calculated for the presence–absence data as standardized effect size (of mpd and mntd, respectively) versus null communities as implemented in Picante to investigate community phylogenetic structures.
DNA as extracted from the water samples was diluted 10- or 100-fold in 1 × Tris-EDTA (TE) buffer, pH 8.0 (Sigma-Aldrich, Munich, Germany) before all qPCR analyses in a LightCycler 480 System (Roche, Mannheim, Germany). Final DNA content in each reaction ranged from 0.1 to 1.8ng depending on the sample. We measured bacterial 16S rRNA gene abundance using a set of community primers (‘Com') adapted from Labrenz et al. (2004) amplifying a fragment spanning positions 519–926 of the E. coli 16S rRNA. Briefly, Com qPCRs (20μl) contained 10μl of LightCycler 480 SYBR Green I master mix (Roche), 0.8μm of each primers (Eurofins MWG), PCR grade sterile water (Roth, Karlsruhe, Germany) and 5μl of sample DNA. An initial activation step of 5min at 95°C was followed by 50 amplification cycles (30s at 95°C, 30 s at 60°C and 30 s at 72°C). Potential formation of primer dimers was determined by melting-point analysis in a range from 65°C to 97°C. No peaks indicating primer dimers were observed in all samples analysed. Quantification of Legionella spp. 16S rRNA gene abundance (‘Leg') was performed using primers L4F (5′-agaaccttacctacccttgacatacagt-3′) and L4R (5′-gacagccatgcagcacctgta-3′) amplifying an 89-bp fragment spanning positions 975–1063 of the L. pneumophila strain Philadelphia 1 16S rRNA gene combined with an internal fluorescent reporter probe L4P (5′-LC610-gtgccttcgggaacactg-BHQ1-3′). Results obtained were comparable with a Sybr green assay using the same primers and amplification conditions as for the Legionella spp. SSCP analysis (data not shown). Leg qPCR reactions (20μl) consisted of 10μl LightCycler 480 Probes Master (Roche), 0.5μm of each primer (Eurofins MWG), 0.2μm of the probe (Eurofins MWG), PCR grade sterile water (Roth) and 5μl of sample DNA. Amplification conditions were 5min at 95°C followed by 50 cycles of 10s at 95°C and 20s at 60°C. Each run contained a 10-fold serial dilution (5 × 101–5 × 105 genome units per reaction) of a commercial quantification standard for genomic L. pneumophila DNA (Minerva Biolabs, Berlin, Germany) for calibration and a non-template control (TE buffer).
We calculated the ratio of Legionella spp. cells to all bacterial cells (RLeg) of each sample by assuming an average 16S copy number of 2.3 cell−1 for freshwater communities and 3 cell−1 for Legionella spp. (Equation 1) with 16Scom 16SLeg and 16Scom16SLeg being the numbers of 16S copies measured by qPCR of Com and Legionella spp., respectively. The value for Legionella spp. cells per litre (NLeg) in each sample was obtained by multiplying total bacterial cell counts per litre (TCC) by the ratio RLeg, assuming further an equal extraction efficiency for the bacterial community and the Legionella community (Equation 2).
During the treatment process, total cell numbers were reduced by about 75% due to flocculation and sand filtration (see decrease from samples GR1 to GR2 and samples ER1 to ER2 in Supplementary Figure S2). This reduction in cell numbers did not affect the community structure as demonstrated previously (Eichler et al., 2006). After chlorination, the cell counts increased to about a level that can be considered typical for finished drinking water, that is, ranging from 2.0 × 108 to 4.0 × 108 cells l−1. This increase was accompanied by a change in the active bacterial community as indicated by RNA-based fingerprints (Eichler et al., 2006).
Seasonal samples of cold and hot drinking water have been analysed previously for their total bacterial communities (Henne et al., 2013). For a comprehensive understanding of the environmental conditions of these samples, the conditions are reiterated here. Monthly samples of cold drinking water comprised 18 samples from May 2008 to October 2009. The mean temperature of the cold water was 12.5°C and varied, depending on the season, between 7.6°C in January and 16.9°C in September (Supplementary Figure S1A). The pH of the cold drinking water varied between 8.2 and 8.8 with a mean of 8.5. During the sampling period, no chlorine was detected (detection limit of 0.1mg l−1) and conductivity had a mean of 142.8±7.5μScm−1. In parallel, hot drinking water was sampled 15 times from September 2008 onwards. The water entered the circular hot water system with 60°C yet, its temperature at the sampling point fluctuated between 49.2°C and 57.9°C with an annual mean of 53.1°C (Supplementary Figure S1B); the pH varied between 7.9 and 8.5 (mean of 8.3); the mean conductivity was 146.4±8.3μScm−1. The number of total bacterial counts of the cold drinking water varied between 0.8 × 108 and 4.8 × 108 cells l−1 with a mean of 2.4 × 108 cells l−1 showing no clear seasonal trend, that is, no maxima or minima with respect to seasons. The dynamics of the bacterial cell counts in hot water followed the cold water dynamics at a lower level (on average by 20%) (Henne et al., 2013).
SSCP fingerprint analysis of Legionella genus-specific amplicons was done on seven bulk water samples of the DWSS of the city of Braunschweig to understand the effects of treatment on the Legionella species composition in drinking water (Figure 1). Fingerprints of raw water from the two drinking water reservoirs (Grane and Ecker reservoir) displayed complex and distinct patterns, indicating a unique composition of diverse Legionella phylotypes in the different raw waters. Complexity of fingerprints of both raw waters was markedly reduced after treatment, recovered in the storage containers (Lewerberg and Lindenberg) and was eventually completely restored to higher levels in the distribution system. Sequence analysis of excised bands confirmed the high diversity of Legionella spp. phylotypes and uniqueness of Legionella communities in the reservoirs and the drinking water at the HZI (Supplementary Table S1). Overall, we identified more than 40 environmental phylotypes of which only two were non-Legionella species (see Figure 2 and asterisks in Supplementary Table S1). These sequencing results demonstrated the validity and specificity of the selected primers for the molecular assessment of Legionella species in freshwater environments.
Phylogenetic analysis of the 16S rRNA gene sequences (Figure 2) revealed the following: (i) a certain phylotype dominated the communities throughout all treatment steps (PTR-01); (ii) some phylotypes from both reservoirs re-emerged at the end of the distribution system (PTR-04 and -05) whereas some others vanished completely (PTR-11, -25 and -26) and (iii) the finished drinking water harboured phylotypes that were not found in either of the reservoirs (PTR-39 and -41) (Supplementary Table S1).
Some of the closest cultured neighbours of the phylotypes found in the raw water samples were related to pathogenic Legionella species according to the Seqmatch results (Supplementary Table S1,Figure 2). In the two raw waters only phylotypes related to L. dumoffii (PTR-01) were in common, whereas PTR-13 (L. erythra), -18 (L. drancourtii) and -11 (L. impletisoli) only occurred in raw water from the Grane reservoir and PTR-36 (L. tucsonensis) and -34 (L. longbeachae) were detected only in the Ecker reservoir. Relative to the other pathogenic Legionella species, L. longbeachae from the Grane reservoir occurred in several bands (PTR-03) in the finished drinking water (Figure 1). The majority of the PTRs listed in Supplementary Table S1 were distributed across the whole phylogenetic diversity of the Legionella genus as shown in Figure 2.
A set of 18 cold drinking water samples, taken in monthly intervals, was analysed by SSCP fingerprints (Supplementary Figure S3A). For a better understanding of the banding patterns on the SSCP gels, a cluster analysis was performed using Pearson correlations (Supplementary Figure S4A). Single seasonal clusters occurred with durations of 3–4 months if an overall similarity of >70% was used.
The abundances of individual PTLs were quantified with the help of GelCompare using the relative intensity of individual bands (Figure 3a). The seasonal dynamics of the relative abundances of Legionella phylotypes defined at about the species level showed 8–14 different PTLs (average=11±1.4) per sample in cold drinking water with abundances ranging from >1% to 53% (Figure 3a). This overall species richness for Legionella, that is, the number of phylotypes above a certain threshold per sample (here: 1.0%), did not show a significant seasonal pattern in synchrony with temperature, precipitation or total bacterial cell counts. Only PTL-01, -06 and -30 were observed to be present above this threshold each month. Although PTL-30 consistently accounted for a major portion (20–50%) of all Legionella phylotypes, changes in abundance of PTL-06 (3–40%) were more pronounced with minima in winter 2008/09 and October 2009 and maxima in July 2008 and May/June 2009. Interestingly, these two major PTLs (-06 and -30) were only detected in cold drinking water. Six other PTLs (-01, -03, -04, -05, -09 and -10) were also found in the hot drinking water during the sampling period (marked with gridded areas in Figures 3a and b and grey dots in Figure 2). Of those, one (PTL-09) emerged in August 2008 and became a major part of the cold drinking water Legionella community, ranging from 7.5% to 24.5% in relative abundance. Only one sequence (PTL-02.5, Figure 4) was identical to L. pneumophila but, it was only observed in a single faint band that occurred in January 2008.
A detailed analysis of partial 16S rRNA gene sequences resulted in a total of 19 Legionella phylotypes in cold water summarized in Supplementary Table S2. The most relevant Legionella species concerning human health is L. pneumophila and therefore, we compared our environmental sequences in detail with the best-known L. pneumophila strains and subspecies (Figure 4). The amplicon of a size of 376bp used in our analyses includes three positions that can vary intragenomically in the genomes of the L. pneumophila strains Philadelphia, Alcoy, Corby, Lens and Paris (positions 187, 261 and 284 of the amplicon). Therefore, the 16S rRNA gene fragment used allowed distinguishing these strains from the two subspecies, L. pneumophila fraseri and pasculleri.
Fifteen samples from hot drinking water were analysed by SSCP fingerprints (Supplementary Figure S3B). The cluster analysis revealed only three clusters ranging from 3 to 8 months (Supplementary Figure S4B). Several sequences of strong SSCP bands present in every hot water sample were identical to L. pneumophila and defined as PTL-02.
In hot drinking water, we observed 6–15 PTLs (average=10.4±2.5) per sample with abundances ranging from >1 to 40% (Figure 3b). PTL-01, -02 and -03 represented a stable core community, which was present each month in a similar composition. These three PTLs comprised always >50% of all phylotypes ranging in summary from 50% to 82% of the total abundances. Strikingly, the PTL-02 (red area in Figure 3b) representing L. pneumophila-like sequences (PTL-02.1 to PTL-02.4, Figure 4) consistently accounted for 8–40% of all Legionella phylotypes in the hot drinking water with an exceptional minimum of 8% in November 2008 and maxima of 40% and 38% in January and June 2009, respectively. In cold drinking water, PTL-02 (sequence PTL-02.5) was observed only at one sampling date (28th of January 2008) and seemed to be slightly different from the PTL-02 sequences derived from hot water (Figure 4). PTL-01, however, displayed a similar abundance as in cold water varying from 24.2% to 44.7% in hot water (compared with 3.5–30%). Remarkably, common PTLs found in both, cold and hot water systems (marked with grey dots in Figure 2 and gridded areas in Figures 3a and b), were generally accounting for 50% of the Legionella communities but this ratio varied more drastically in cold than in hot water.
In hot water, the detailed analysis of the 16S rRNA gene sequences resulted in a total of 24 Legionella phylotypes (Supplementary Table S2). Six of the hot water PTLs were in common with cold water and one PTL (-02) clustered within L. pneumophila (Figures 3 and and4).4). Based on these high sequence similarities, we think that both types of finished drinking water contained bacteria belonging to the species L. pneumophila, but they are substantially more abundant in hot than in cold drinking water.
Comparison of Legionella community compositions in hot and cold drinking water was done by detailed cluster analysis (Figure 5). These analyses confirmed the general pattern of the fingerprints derived from SSCP gels. Cold water communities were substantially different from the hot water communities as demonstrated by the dendrogram using a Bray-Curtis distance matrix of untransformed abundance values (Figure 5a). Ordination by non-metric multidimensional scaling (NMDS) of PTL abundance and phylogenetic distance between phylotypes showed, like the SSCP fingerprints, more and smaller clusters in cold than in hot water communities when applying a similarity threshold of 70% (Figure 5b).
The Legionella community comprised on average 0.67% (±0.58) of the cold water bacterial community corresponding to an average cell number of 1.7 × 106 cells l−1 (Supplementary Figure S6). These genus-specific cell numbers were based on quantification by real-time PCR with primers targeting the genus Legionella and the total bacterial cell number of the water sample as detailed in Materials and methods. The Legionella community of the hot water comprised a significantly larger fraction, that is, on average 2.4% (±1.5), corresponding to 3.8 × 106 cells l−1. These numbers indicated a substantial increase of the Legionella fraction of the total bacterial community with respect to the relative abundance and the absolute cell numbers from cold to hot water.
Rank-abundance curves of Legionella communities from cold and hot water did not differ substantially and variation for both Legionella regression analyses was high as indicated by their relatively low coefficients for determination (Supplementary Figure S5). Additionally, mean Legionella species richness per sample did not significantly differ between both environments (Table 1) although total Legionella species richness over the whole sampling period was slightly higher in hot water (cold water: n=17, hot water: n=20). Despite these similarities of mean species richness, both environments differed in other metrics of alpha diversity. Shannon and (inverse) Simpson index of the Legionella communities were significantly higher for cold water samples (Table 1) as observed also for the bacterial communities. Common indices for beta diversity and evenness coherently showed significantly higher values for the Legionella community in cold water, which is in line with its more dynamic community structure (Table 1, Figure 3) (Henne et al., 2013). Phylogenetic distance (pd) was slightly higher for cold water Legionella, and also the negative values for mean nearest taxon distance (mntd) and mean pairwise distance (mpd) indicated that PTLs in cold water were more distantly related to each other (Table 1) (Webb, 2000). In other words, hot water PTLs were clustering closer to each other.
Taking phylogenetic relationships and relative abundances of single phylotypes into account NMDS ordination revealed dynamics of bacterial and Legionella communities (Figure 6). For better illustration of clusters, ordination plots are shown separately for both types of drinking water since their communities shared only few phylotypes. Cold water bacterial communities clustered into three groups of four to seven sampling dates (Figure 6a). Clusters were aggregations of subsequent dates with samples 6 and 14 being outliers. These outliers had been identified as turning points between winter and summer phases of the total bacterial community (Henne et al., 2013). Similarly, Legionella communities from the same samples clustered into four groups of three to four sampling dates with two outliers (Figure 6b). Although clusters contained mainly subsequent dates, this pattern was not as strictly followed here, while samples 1 and 6 were outliers. Clusters were mainly characterized by the constant decrease in the abundance of PTL-30 and the constant increase in PTL-09 during the sampling period (Figure 3a).
Clusters of hot water samples looked very different from the cold water clusters. Concerning the bacterial communities all sample dates clustered into one single group, except for one outlier (Figure 6c). This reflected the rather stable community composition dominated by single phylotypes from five different taxonomic groups (Henne et al., 2013). Similarly, most of the Legionella communities from hot water clustered into one single group, but here two outliers were identified next to one smaller additional cluster of samples 20 and 22 (Figure 6d). This clustering also reflected a more constant species composition, mainly due to steadily high abundances of the major PTLs (Figure 3b). Overall, dynamics of Legionella communities in drinking water behave similar to the one of the most abundant bacterial phylotypes as deduced from diversity indices and clustering patterns in cold and hot drinking water. However, differences in the sample composition of single clusters and phylogenetic structure could indicate a selection pressure specific for Legionella species.
Since the temperature regime is an important controlling factor of Legionella growth and survival, the abundance of the Legionella cell numbers per litre was compared with the temperature observed in the respective sample. For cold water, the Legionella cell numbers did not show a clear trend within the range of the observed in situ temperatures from 7.6°C to 16.9°C (Figure 7a). In addition, specific cell numbers of single phylotypes were calculated using the fraction of the respective phylotype derived from SSCP analyses and the respective total Legionella cell number of a given sample. For single phylotypes of the total Legionella community also no correlation to temperature was observed (Supplementary Table S3). By contrast, for hot water, there was a significant increase in the total Legionella abundances from 49.2°C to 57.9°C by a factor of about three (Figure 7b). A positive response of cell numbers to temperature was also observed for the two most abundant phylotypes (Supplementary Table S3). This increase with temperature is shown in detail for the most abundant phylotypes PTL-01 and PTL-02 closely affiliated with L. longbeachae and L. pneumophila, respectively (Figure 7c). For these phylotypes, an increase in cell numbers by an order of magnitude from 49.2°C to 57.9°C was observed, indicating a preference for these high temperatures and the thermophilic nature of these phylotypes.
The taxonomic resolution and the affiliation of the single 16S rRNA sequences with cultured Legionella species has to be considered to understand the relevance of the obtained results for the ecology of this genus. SSCP fingerprints provide phylogenetic and abundance information of single taxa using partial 16S rRNA sequence data and relative peak intensities of individual bands of the fingerprint. Our consensus phylotypes, summarized in Supplementary Tables S1 and S2, can be considered to cover a broad set of different species of the genus Legionella. Figure 2 provides an overview about the phylogenetic positions of all 76 PTLs observed in a total of 40 samples from three different years of the studied DWSS and demonstrates the enormous phylogenetic breadth and depth of the Legionella species present. This finding corroborates with other studies of the environmental occurrence of Legionella species in freshwater environments using cultivation-independent approaches (Calvo-Bado et al., 2003; Riffard et al., 2001; Brooks et al., 2004). How the observed PTLs relate to individual cultured Legionella species is only clear for L. pneumophila (Figure 4). The other PTLs could be divided into two different types: (i) PTLs closely related to cultured species (for example, PTR-41 and PTL-13) and (ii) PTLs belonging to deeper branches with no phylogenetic relationship to cultured species (for example, the PTLs clustered around PTL-012 and PTL-05). The first type of PTLs might stem from strains of the closely related species and the observed sequence variation can be considered to be due to micro-heterogeneity of the 16S rRNA gene sequences as demonstrated for L. pneumophila (Figure 4). The second type of PTLs could relate to the many environmental Legionella species that have not yet been cultured and identified (Costa et al., 2005; Wullings and van der Kooij, 2006; Declerck et al., 2007a; Wullings et al., 2011).
In our DWSS, treatment of the raw water reduced substantially the Legionella species diversity to only one resilient and dominant phylotype (PTL-01) occurring after treatment and in the storage containers (Figure 1). However, in concordance with the whole bacterial communities (Eichler et al., 2006), diversity of Legionella spp. was restored along the DWSS. A similar reduction and regrowth of Legionella spp. has been observed in other chlorinated DWSS (Whiley et al., 2014). Interestingly, the occurrence of phylotypes not detected in the raw waters suggests the selection of Legionella species well adapted to our DWSS. This selection pressure could result from low-nutrient content, presence/absence of certain host protozoa or bacterial competitors and effects of chlorination. Furthermore, invasion of Legionella species from mature biofilms of the DWSS has to be taken into consideration (Lau and Ashbolt, 2009; Abdel-Nour et al., 2013). This invasion from biofilm might be a key mechanism for the increase in Legionella species in bulk water because the ratio of biofilm surface to water volume increases on its way from the storage container to the tap at the HZI where the highest number of Legionella species occurred (Figure 1). Notably, no phylotype identical or similar to L. pneumophila could be detected in raw water and along the water treatment process. In contrast, the phylotype related to L. pneumophila (PTL-02) was only detected once in cold drinking water, but was always present at substantially higher abundances in hot drinking water (Figure 3).
The seasonal dynamics of bacterial community composition in cold and hot water of our DWSS have been recently described in detail at the level of the most dominant bacterial phylotypes (Henne et al., 2013). This study showed by comparing rank-abundance curves that on average the bacterial communities in cold water had a more even species composition than in hot water (see Figure 4 in Henne et al., 2013). Accordingly, total bacterial species richness was significantly higher in cold water (n=55) than in hot water (n=44) (Henne et al., 2013). Here we analysed the same set of samples but focusing only on members of the genus Legionella.
Seasonal dynamics of the Legionella community were observed neither in cold nor in hot drinking water. Statistical analyses showed a closer relatedness of Legionella communities of subsequent months. This is consistent with observations for the total bacteria community of the hot water in our previous study, while for the cold water seasonal dynamics were observed for the whole bacterial community (Henne et al., 2013).
The Legionella community composition of cold and hot drinking water showed that both systems harbour phylogenetically quite distinct communities, but 6 of the major 35 PTLs were shared (Figure 3, Supplementary Table S2). The observed minute differences between the individual sequences of these common PTLs of cold and hot water (Figure 4) could indicate that there were different strains in the different types of water which were better adapted to the respective temperature. High-resolution genotyping analyses of these water samples as performed for L. pneumophila could elucidate such differences on the strain level indicated by the high degree of micro-heterogeneity observed in the 16S rRNA sequences (Kahlisch et al., 2010).
The structure of the Legionella communities in both types of water was dissimilar as suggested by the corresponding statistical analysis (Figure 5). Such a pronounced discrepancy has also been shown for the total bacterial community of cold and hot drinking water (Henne et al., 2013). The Legionella communities of the hot water showed a reduced overall diversity (for example, Shannon index) and less phylogenetic distance among PTLs in comparison with cold water, despite comparable richness (Table 1, Supplementary Figure S5). The dynamics of the Legionella communities of both types of water were also substantially different as revealed by the NMDS ordination plots (Figures 6b and d). These differences in the community dynamics could stem from the different environmental conditions and selection pressure and their seasonal variability in the two types of water.
Hot water production in our DWSS is a rather rapid process: hot water returning from the distribution system and cold water are co-heated at about 63°C for about 1 h. During this short time span, the cold water bacterial community decays by about 95% thereby providing nutrients for regrowth (Henne et al., 2013). Heating-induced changes of the Legionella community were well pronounced, but still less substantial than those observed for the whole bacterial community where different thermotolerant and thermophilic species dominated the overall hot water community (Henne et al., 2013). This indicates an intrinsic potential to adapt to a wide range of temperature regimes within the genus Legionella and we assume that thermophilic phylotypes have an important role for the following reasons. First, the total abundance of members of the genus Legionella increased relatively to the total bacterial community but also in absolute terms from 1.7 × 106 to 3.8 × 106 cells l−1 from cold to hot water (Supplementary Figure S6). Second, the cell numbers for the genus Legionella increased by a factor of 3 along the temperature range observed for the analysed samples from 49.2°C to 57.9°C (Figure 7b). Third, this positive correlation with temperature was confirmed among others (PTL-21, -22 and -24, data not shown) for the most abundant phylotypes PTL-01 and PTL-02 that were most closely affiliated with L. longbeachae and L. pneumophila, respectively (Figure 7c, Supplementary Table S3). In contrast, no clear temperature effect was seen for the cold water Legionella community. Thus we could demonstrate that a set of Legionella species, including L. pneumophila, were able to grow at temperatures above 50°C, and survive or grow until 63°C.
Currently, no Legionella species are known that are able to grow at temperature above 50°C (Stout et al., 1986; Steinert et al., 1998; Vervaeren et al., 2006). Especially L. pneumophila and L. longbeachae have been extensively studied, but although numerous isolates have been obtained among others from hydrothermal springs and spas at temperatures between 40°C and 60°C, indicating thermotolerant characteristics of Legionella species, to our knowledge growth above 45°C has not been documented until now (Veríssimo et al., 1991; Ghrairi et al., 2013). Better survival and viability traits have been described for L. pneumophila strains isolated from a shock heated (70°C for 30min) hospital DWSS and a Tunisian therapeutic spa, but growth above 45°C was not tested (Allegra et al., 2011; Ghrairi et al., 2013). Adaptations, spontaneous mutations or horizontal gene transfer from thermophilic Legionella species or other thermophilic bacteria of the hot water community could have supported this development (Lindsay, 1995). It also appeared that thermophilic traits could readily be gained and lost as shown for Bacillus species (Hobbs et al., 2012). High levels of horizontal gene transfer have been shown for members of the genus Legionella within species and at the genus level by inter- and intra-species genome comparisons rendering it a conceivable means for acquisition of thermophilic traits (Gomez-Valero et al., 2011, 2014). Therefore, the development of thermophilic genotypes could be considered for L. pneumophila but also for other Legionella species.
Though the whole genus of Legionella is considered as having a potential to cause disease, only a very restricted set of species was shown to cause major health problems with L. pneumophila and L. longbeachae being the most important candidates (Phin et al., 2014; Mercante and Winchell, 2015). In this respect, the hot water system could be considered as a higher health risk than the cold water due to the relatively high abundance of L. pneumophila PTL-02. The use of hot water is in general perceived as a potential public health risk (Borella et al., 2005b; Leoni et al., 2005; Mouchtouri et al., 2007; Phin et al., 2014). However, all these hot water studies did not assume the growth of pathogenic Legionella species in hot water systems above 50°C, though some of their observations may indicate it (Borella et al., 2005b; Leoni et al., 2005).
The general perception of a reduced risk of legionellosis when water is continuously heated between 50°C and 60°C may suggest that thermophilic Legionella do not pose a major health threat. However, it cannot be ruled out that the thermophilic genotypes of pathogenic species, like L. pneumophila, as demonstrated for our hot water systems are of relevance for public health. Therefore, the aspect of high temperature adapted genotypes may deserve further detailed studies with respect to their clonal nature, physiology and virulence traits including the attempt to isolate these genotypes.
Only a restricted set of genotypes of L. pneumophila is virulent and able to cause disease (Sobral et al., 2011; Khan et al., 2013; Phin et al., 2014). On the other hand, DWSS can be considered as highly diverse ecosystems providing a wealth of niches for selection and potentially adaptation or even evolution of specific genotypes as shown by the genotype pattern in large and small water supply systems (Sobral et al., 2011; Khan et al., 2013; Rodríguez-Martínez et al., 2015). Specific genotypes may get established in DWSS that show distinct ecological preferences, for example, for temperature, and a distinct abundance as shown by Rodríguez-Martínez et al. (2015). The relevance of the genotypes for health can only be finally assessed by isolate-based studies in macrophage assays (Epalle et al., 2015; Mercante and Winchell, 2015). To analyse the genotype distribution in a DWSS, high-resolution genotyping methods have to be applied to isolates and/or environmental DNA (Gaia et al., 2005; Ratzow et al., 2007; Kahlisch et al., 2010; Sobral et al., 2011). Strain-based investigations applying genotyping, physiological and virulence assays accompanying the molecular study may link the Legionella diversity to the genotype pattern of L. pneumophila, enabling assessment of their ecotype and potential health risk.
In conclusion, we demonstrated in our DWSS that the water treatment of two raw waters reduced the complexity of their Legionella communities' strongly but it did not fully eradicate the genus. Consequently, Legionella communities gradually re-established complexity along the DWSS resulting in a changed species composition better adapted to the respective conditions. Interestingly, Legionella community dynamics did not display a true seasonal trend yet, its species composition changed gradually due to factors that could not yet be fully identified. Although relative abundance of Legionella spp. stayed below 1% of the total bacterial community, cell numbers of more than 1.5 × 106 cells l−1 were reached exceeding the currently tolerated levels of Legionella colony forming units per litre by two orders of magnitude. Yet, both methods cannot provide a true risk assessment due to the complex lifestyle of Legionella spp. (Robertson et al., 2014). During their parasitic and planktonical life phases, Legionella cells pass through a variety of developmental stages and not all of them allow the bacteria to be cultured on agar plates (for example, VBNC states) or to be infectious. Molecular analyses on the other hand detect theoretically all target genes above a detection limit, but do not discriminate between live and dead cells. The heating to 63°C further altered the drinking water Legionella community substantially. As for the whole bacterial community heating caused a shift to a thermophilic species composition and up to a threefold increase in Legionella cell numbers. Our findings document an adaptation of the community to the elevated temperatures and active growth of Legionella spp. at temperatures above 50°C. Notably, cell numbers of L. pneumophila phylotypes increased with temperature, possibly a major concern for drinking water safety and public health. These thermophilic L. pneumophila populations deserve extensive future research using the full array of cellular and molecular methods available in microbiology.
This work was supported by funds from the Deutsche Forschungsgemeinschaft (DFG-project HO-930/5-1) and the EU project (No. 311846) AQUAVALENS. We thank Julia Strömpl, Josefin Koch and Verena Maiberg for their skilful technical support. Axel Mohr and Monika Pape are acknowledged for support with the technical devices of the DWSS of the HZI. Karsten Henne and Leila Kahlisch are acknowledged for valuable support with respect to total bacterial cell counts, primer design and SSCP analysis. We are very grateful to the constructive comments of two anonymous reviewers.
The authors declare no conflict of interest.
Supplementary Information accompanies this paper on The ISME Journal website (http://www.nature.com/ismej)