Skip to main content
Browse Subject Areas

Click through the PLOS taxonomy to find articles in your field.

For more information about PLOS Subject Areas, click here.

  • Loading metrics

Tracking Down Antibiotic-Resistant Pseudomonas aeruginosa Isolates in a Wastewater Network

  • Céline Slekovec,

    Affiliations Service d'Hygiène Hospitalière, Centre Hospitalier Universitaire, Besançon, France, Unité Mixte de Recherche 6249 Chrono-environnement, Université de Franche-Comté, Besançon, France

  • Julie Plantin,

    Affiliations Service d'Hygiène Hospitalière, Centre Hospitalier Universitaire, Besançon, France, Unité Mixte de Recherche 6249 Chrono-environnement, Université de Franche-Comté, Besançon, France

  • Pascal Cholley,

    Affiliations Service d'Hygiène Hospitalière, Centre Hospitalier Universitaire, Besançon, France, Unité Mixte de Recherche 6249 Chrono-environnement, Université de Franche-Comté, Besançon, France

  • Michelle Thouverez,

    Affiliations Service d'Hygiène Hospitalière, Centre Hospitalier Universitaire, Besançon, France, Unité Mixte de Recherche 6249 Chrono-environnement, Université de Franche-Comté, Besançon, France

  • Daniel Talon,

    Affiliations Service d'Hygiène Hospitalière, Centre Hospitalier Universitaire, Besançon, France, Unité Mixte de Recherche 6249 Chrono-environnement, Université de Franche-Comté, Besançon, France

  • Xavier Bertrand,

    Affiliations Service d'Hygiène Hospitalière, Centre Hospitalier Universitaire, Besançon, France, Unité Mixte de Recherche 6249 Chrono-environnement, Université de Franche-Comté, Besançon, France

  • Didier Hocquet

    Affiliations Service d'Hygiène Hospitalière, Centre Hospitalier Universitaire, Besançon, France, Unité Mixte de Recherche 6249 Chrono-environnement, Université de Franche-Comté, Besançon, France


The Pseudomonas aeruginosa-containing wastewater released by hospitals is treated by wastewater treatment plants (WWTPs), generating sludge, which is used as a fertilizer, and effluent, which is discharged into rivers. We evaluated the risk of dissemination of antibiotic-resistant P. aeruginosa (AR-PA) from the hospital to the environment via the wastewater network. Over a 10-week period, we sampled weekly 11 points (hospital and urban wastewater, untreated and treated water, sludge) of the wastewater network and the river upstream and downstream of the WWTP of a city in eastern France. We quantified the P. aeruginosa load by colony counting. We determined the susceptibility to 16 antibiotics of 225 isolates, which we sorted into three categories (wild-type, antibiotic-resistant and multidrug-resistant). Extended-spectrum β-lactamases (ESBLs) and metallo-β-lactamases (MBLs) were identified by gene sequencing. All non-wild-type isolates (n = 56) and a similar number of wild-type isolates (n = 54) were genotyped by pulsed-field gel electrophoresis and multilocus sequence typing. Almost all the samples (105/110, 95.5%) contained P. aeruginosa, with high loads in hospital wastewater and sludge (≥3×106 CFU/l or/kg). Most of the multidrug-resistant isolates belonged to ST235, CC111 and ST395. They were found in hospital wastewater and some produced ESBLs such as PER-1 and MBLs such as IMP-29. The WWTP greatly reduced P. aeruginosa counts in effluent, but the P. aeruginosa load in the river was nonetheless higher downstream than upstream from the WWTP. We conclude that the antibiotic-resistant P. aeruginosa released by hospitals is found in the water downstream from the WWTP and in sludge, constituting a potential risk of environmental contamination.


Pseudomonas aeruginosa is a rod-shaped Gram-negative aerobic bacterium that can grow in many niches, but prefers moist environments. It is found in both low-nutrient or oligotrophic environments and highly nutritious environments, such as sewage and the human body.

P. aeruginosa is a common hospital-acquired pathogen of the respiratory and urinary tracts, in all hospital departments, but particularly intensive care units, in which 15% of healthcare-associated infections are attributed to this pathogen [1]. Hospital outbreaks linked to multidrug-resistant strains of P. aeruginosa are widely reported [2][5]. The intrinsic resistance of P. aeruginosa to many classes of antibiotics and its capacity to acquire resistance to almost all effective antibiotics during treatment render infections with this microorganism very difficult to treat [6][8]. Multidrug-resistant P. aeruginosa is thought to emerge principally at hospitals, where large amounts of antibiotics are used [9]. Antibiotic resistance in P. aeruginosa mostly results from chromosomal mutations, but may also be acquired by horizontal gene transfer [10]. Resistance to β-lactams is of particular concern in clinical practice. High-level resistance to these compounds is achieved by AmpC cephalosporinase overproduction or by the production of acquired β-lactamases with an extended spectrum (i.e. ESBLs, MBLs and extended-spectrum oxacillinases) [11].

P. aeruginosa also causes community-acquired infections, including folliculitis and ear infections acquired by recreational exposure to water containing the bacterium and keratitis, particularly in patients who wear contact lenses. Although some P. aeruginosa strains are shared by cystic fibrosis patients, the source of the contamination remains unknown and could include the natural environment (e.g. soil and water) as reservoir.

Typically, the wastewater from urban sewerage systems (containing rainwater, hospital and urban wastewater) is treated at a wastewater treatment plant (WWTP), to generate clean effluent for discharge into rivers and of sludge, which may be used as a fertilizer. Antibiotic-resistant P. aeruginosa (AR-PA) strains are found in the effluent of WWTPs and in the river water downstream from these plants [12]. However, the source of these resistant bacteria has yet to be clearly established. The potential dissemination of P. aeruginosa from hospitals to natural environments may contribute an increase in the number of community-acquired infections with multidrug-resistant pathogens.

We evaluated the risk of AR-PA dissemination from hospitals to the environment. We quantified the P. aeruginosa load throughout the wastewater network and determined the antibiotic resistance profile of the isolates obtained, focusing in particular on enzyme-based mechanisms of resistance to β-lactams. We then determined the genotype of antibiotic-resistant isolates, to facilitate the tracking of their spread from the hospital to the environment. We conclude that the AR-PA strains released by hospitals are found in the water downstream from the WWTP and in sludge, constituting a potential risk of environmental contamination.

Materials and Methods

Study setting

This study was carried out in the city of Besançon, in eastern France (130,000 inhabitants). The WWTP studied serves approximately 120,000 people and had a mean hydraulic load in 2011 of 30,000 m3 per day. The effluent treated by the plant includes effluents from two University hospital sites, with 800 and 400 beds, urban wastewater and rainwater (Figure 1). The water is treated by a sequence of three typical treatments (sedimentation, biological content degradation and effluent polishing) before sludge production and the discharge of the treated effluent into the river. Of the 7,500 metric tons of sludge produced each year, 4,500 metric tons are used as fertilizer. The river upstream from the WWTP contained treated water originating from medical facilities 80 km upstream from the city of Besançon. Mean monthly rainfall was 46 mm during the study period, and 88 mm over the last decade.

Figure 1. Map of the study area.

The large map indicates the precise location of the sampling sites, with the inset map indicating the location of the area in France.

Wastewater sampling

Samples were collected from 11 sites distributed throughout the wastewater network of the city (Figure 1). Each collecting point was sampled weekly, over a 10-week period, between January and April 2011. We collected (i) wastewater from the two sites of our hospital (containing only hospital effluent and rainwater), (ii) three urban wastewater samples independent of hospitals and healthcare facilities. We also collected samples within the WWTP: (iii) untreated water containing urban and hospital wastewater (n = 1), (iv) treated water before its discharge into the river (n = 2; the daily samples consisted of pools of aliquots taken from each 10 m3 volume of water) and (v) the anaerobically digested sludge ready for spreading on farm fields (n = 1). We also collected samples of river water (vi) upstream and (vii) downstream from the WWTP.

P. aeruginosa load determination

Samples were analyzed within eight hours of collection. We quantified P. aeruginosa in heavily loaded samples (urban wastewater, untreated water, sludge and hospital wastewater), by serial dilution method, after appropriate dilution in sterile water. A 100-µl aliquot of each diluted sample was plated on a Pseudomonas-specific agar plate (CN/agar, Bio-Rad, Marnes-La-Coquette, France). The P. aeruginosa load of lightly contaminated samples (treated water and river water) was assessed by the membrane filtration method. A 100-ml aliquot of the water to be tested was passed through a filter with 0.45-µm pores, which was then placed on a CN/agar plate. CN/agar plates were incubated for 48 h at 37°C. P. aeruginosa colonies were initially detected by standard microbiology methods (i.e. colony morphology, positive oxidase reaction, pigment production). Identification was then confirmed with a biochemical test (ID 32 GN, Biomérieux, Mercy l'étoile, France). We analyzed a maximum of five colonies per plate, selected on the basis of colony morphology, and these colonies were stored in brain heart infusion broth supplemented with 20% glycerol at −80°C until analysis.

Bacterial clearance rates

The clearance rate at the WWTP was determined as follows:

Antimicrobial susceptibility testing and β-lactamase identification

We aimed to assess the diversity of the resistance profiles within each sample. We used colony morphology methods, despite the limitations of this method (maximum of five morphotypes per sample. We assessed the activity of 16 antibiotics from four different classes (non-carbapenem β-lactams: cefepime, piperacillin, piperacillin-tazobactam, cefotaxime, ticarcillin, ticarcillin-clavulanate, ceftazidime, aztreonam; carbapenems: meropenem, imipenem; aminoglycosides: gentamicin, tobramycin, amikacin; fluoroquinolones: ciprofloxacin) against the selected P. aeruginosa isolates by the disk diffusion method, as recommended by the Antibiogram Committee of the French Society for Microbiology [13]. Three resistance phenotypes were defined: ‘wild-type’ (susceptible to all the tested antibiotics), ‘resistant’ (not susceptible to antibiotics from one or two classes), and ‘multidrug-resistant’ (not susceptible to antibiotics from three or more classes). We also identified ESBLs and MBLs in isolates resistant to third-generation cephalosporins, by the phenotypic method described elsewhere [14]. For isolates considered positive by this approach, the enzymes involved were identified by PCR and sequencing with primers targeting ESBL- and MBL-encoding genes [15].

Genotyping by pulsed-field gel electrophoresis (PFGE)

The clonality of strains was investigated by PFGE, with DraI digestion, as previously described [16]. The electrophoresis was performed at 14°C and 5.5 V/cm using the CHEF DR III apparatus (Bio-Rad Laboratories, Hercules, Calif.) in 15-cm by 20-cm 1% agarose gels (Life Technologies, Saint Aubin, France). We used two successive sequences of electrophoresis. The first sequence lasted 12 h with a constant switch time of 20 s. The second sequence lasted 17 h with a switch time increasing from 5 s to 15 s. Samples of SmaI-restricted DNA from Staphylococcus aureus NCTC 8325 were included in each run as an internal reference. The banding patterns were analyzed by scanning photographic negatives. GelCompar software was used for cluster analysis (Applied Maths, Kortrijk, Belgium). Each strain was first compared with all other strains. The Dice correlation coefficients were grouped and the UPGMA clustering algorithm was used to depict the groups as a dendrogram. Pulsotypes (PTs) were defined according to international recommendations [17].

Genotyping by multi-locus sequence typing (MLST)

MLST was performed according to the protocol of Curran et al. [18], as modified by van Mansfeld et al. [19]. Nucleotide sequences were determined for internal fragments of the acsA, aroE, guaA, mutL, nuoD, ppsA and trpE genes, on both strands, and were compared with sequences in the P. aeruginosa MLST website ( for the assignment of allele numbers and sequence types (ST).

Analysis of MLST data

We investigated the evolutionary relationship between isolates with the minimal spanning tree (MST) algorithm, which is based on allelic profiles. The MST algorithm is a graphical tool that links the nodes by unique minimal paths in a given dataset, i.e. the total summed distance of all the branches is minimized [20]. The algorithm uses the ST with the highest number of single locus variants (SLVs) as a root node, from which it derives the other STs. Using a stringent definition of 5/7 shared alleles, MST then connects all the strains and links all related STs into clonal complexes. Singletons were thus defined as STs with at least three allelic mismatches with all other STs.

Ethics statement.

This study was approved by the ‘Comité d'Etude Clinique’ ethics committee of Besançon Hospital, Besançon, France. All the water and sludge samples came from public areas and facilities. All necessary permits were obtained by Christian IMPERAS, Technical Director of Water Supply and Water Treatment Service of the City of Besançon. We confirm that the location is not privately-owned or protected in any way. We confirm that the field studies did not involve endangered or protected species.

Statistical analysis

Continuous variables were compared in non-parametric Kruskal-Wallis tests and categorical variables were compared in Pearson's Chi-squared test. All tests were two-tailed, and a p-value of less than 0.05 was considered statistically significant.


P. aeruginosa load of the samples

Over the study period, we processed 110 samples, 105 (95.5%) of which tested positive for P. aeruginosa. The P. aeruginosa load at the sampling locations is detailed in Figure 2. The P. aeruginosa load of hospital wastewater was 25 times higher than that of urban wastewater (4.46×106 vs. 0.18×106 CFU/l, respectively; p = 0.0001). The effluent treatment carried out by the WWTP resulted in an overall P. aeruginosa clearance rate of 94.0% (2.5×105 CFU/l in untreated water versus 1.1×104 CFU/ml in treated water; p = 0.0001). However, wastewater treatment concentrated P. aeruginosa in the sludge, resulting in a high load (2.95×106 CFU/kg). The P. aeruginosa load in the river downstream from the WWTP was significantly higher than that in the river upstream from the WWTP (128 versus 27 CFU/l, respectively, p = 0.0012).

Figure 2. P. aeruginosa load of the water and sludge at the various sampling points.

The proportion of the isolates with each resistance profile (white: wild-type; gray: resistant; black: multidrug-resistant) is shown. a The bacterial load in the sludge is expressed in CFU per kg.

Resistance profile analysis

Based on colony morphology (see above), we selected 238 isolates for further testing: 38 were isolated from hospital wastewater, 70 from urban wastewater, 88 from the WWTP (27 from untreated water, 49 from treated water and 12 from sludge) and 42 were isolated from the river (13 upstream from the WWTP, 29 downstream from the WWTP). We classified 182 of these 238 isolates as wild-type, 39 as resistant and 17 as multidrug-resistant. Wild-type and resistant strains were ubiquitous, whereas multidrug-resistant strains were found only in hospital wastewater, treated water and the river. For identification of the ESBLs and MBLs harbored by P. aeruginosa in the wastewater network, we characterized the enzymatic mechanism of resistance to β-lactams in the 11 isolates resistant to third-generation cephalosporins (cefepime and/or ceftazidime). Eight of these isolates overproduced the chromosomally encoded cephalosporinase AmpC as the sole enzyme conferring resistance to β-lactams. Two P. aeruginosa isolates from hospital wastewater produced the ESBL PER-1. One isolate from treated water within the WWTP produced the MBL IMP-29 (Figure 3).

Figure 3. Minimal spanning tree analysis of P. aeruginosa strains based on MLST data and resistance profiles.

The proportion of isolates with each antibiotic resistance profile is indicated for each ST. Each dot represents a single ST, with a diameter proportional to the number of isolates (see frame). The relationships between strains are indicated by the connections between the dots and the lengths of the branches linking them. The gray areas surround STs belonging to the same clonal complex. * One ST235 isolate (from hospital wastewater) produced the ESBL PER-1 and another (from the water treated by the WWTP) produced the MBL IMP-29. **: One ST1080 isolate (from hospital wastewater) produced PER-1.


We determined the PFGE profile of all 56 non-wild-type isolates (39 resistant and 17 multidrug-resistant isolates) and a similar number (54 of the 182) of wild-type isolates selected at random. Of the 110 P. aeruginosa isolates analyzed, 32 were from hospital wastewater, 26 were from urban wastewater, 36 were from the WWTP and 16 were from the river (see details in the Table S1). This analysis yielded 80 different PTs, 65 of which were unique (Table S1). Fifteen multiple PFGE patterns were each found in two to eight strains: nine PTs included two strains, two PTs included three strains, two PTs included four strains, one PT included five strains and one PT included eight strains.

As PFGE typing is more discriminatory than MLST, we assumed that all the isolates with a given PT belonged to the same ST. We therefore determined the MLST profiles of the 54 PTs including at least one resistant or multi-resistant isolate. These 54 PTs included 81 isolates: 25 wild-type and all 56 resistant or multidrug-resistant isolates. These PTs belonged to 41 different STs. Three major STs were identified: ST235 (including 13 isolates from hospital wastewater and WWTP); ST395 (including eight isolates from the various sampling points of the wastewater network) and ST253 (including six isolates from the river and the WWTP) (Figure 4). We determined the clonal relationship between STs by the MST method based on allelic profile [21]. Two allelic mismatches were allowed for group definition, as in group definition with eBURST. We represented the MST of the isolates with respect to their resistance profiles (Figure 3) or their origins (Figure 4). The 41 STs identified were distributed into 35 singletons (73 isolates) and two clonal complexes of six isolates (CC111, which included ST111 and ST966; and CC446, which included ST446 and ST296). The details of the STs (antibiotic resistance profile and origin) are provided in Table S1.

Figure 4. Minimal spanning tree analysis of P. aeruginosa strains based on MLST data and isolation sites.


P. aeruginosa in the wastewater network

More than 95% of the water samples tested positive for P. aeruginosa, demonstrating the presence of this species throughout the wastewater network (Figure 2). The clearance rate at the WWTP was high (94%; Figure 2), but we nevertheless found resistant and multidrug-resistant isolates in the treated water before its release in the river and in the sludge produced by the WWTP. Of particular interest, the treated water was found to contain an isolate producing the MBL IMP-29 recently described at our hospital [22]. The PT of the clinical isolates described by Jeannot et al. differed from that of the isolate in our series (data not shown), suggesting horizontal transfer of the resistance gene. Such resistance transfer has clearly been described in WWTPs, in the absence of antibiotic selection [23]. We found an unexpectedly high concentration of P. aeruginosa in the sludge produced by the WWTP (2.95×106 CFU/kg), a concentration within the range generally found in hospital wastewater (Figure 2). This sludge is used as a fertilizer and is applied to the soil directly, without dilution. Thus, treated water and sewage sludge may constitute a potential risk of environmental contamination with AR-PA.

P. aeruginosa release from the hospital

The release of AR-PA into the environment by hospitals is a controversial issue. P. aeruginosa isolates resistant to ciprofloxacin or producing VIM-type MBLs have been obtained from wastewater and hospital discharge sites [12], [24], [25]. By contrast, a pilot study showed that our hospital did not release AR-PA into the environment [26]. However, hospital wastewater is a highly selective environment that may contribute to the maintenance of resistant bacteria discharged into the natural environment [27], [28]. This study was designed to address these issues. The P. aeruginosa load was found to be significantly higher in hospital wastewater than in urban wastewater, consistent with previous findings [12]. This is particularly important given the much higher dilution phenomenon in hospitals than in the community (1,000 l of wastewater per bed per day versus only 150 l per inhabitant per day in the community). As expected, the STs found in hospital effluent (ST111, ST235, ST395 and ST446) had all previously been isolated from patients hospitalized in our medical facility [11]. We have shown that most of the multidrug-resistant isolates from hospitals belong to a few clonal types [11]. We therefore hypothesized that, in this series, the high frequency of resistance to antibiotics was due to the overrepresentation of certain resistant clones. Resistant isolates from hospital wastewater were genotyped and most were found to belong to ST235, ST395, ST309, ST273, CC111 and CC446 (Table S1). The overall frequency of resistant P. aeruginosa isolates was higher in hospital wastewater than among isolates obtained directly from clinical samples (Bertrand X., personal data). This suggests that the hospital wastewater environment (containing antibiotics, disinfectants and heavy metals, in particular) [29] favors these antibiotic-resistant clones over susceptible clones.

Tracking down antibiotic-resistant P. aeruginosa from the hospital

We assessed the fate of AR-PA clones released into the wastewater network by the hospital, including their presence in the WWTP, downstream river water and sludge. Genotyping of the resistant isolates throughout the network showed that three STs or clonal complexes present in the hospital wastewater (ST235, ST395, and CC111) were also present in the WWTP or the river. ST235 was represented by 13 resistant and multidrug-resistant strains, mostly isolated from hospital wastewater (n = 10), but also found in untreated water (n = 1) and in treated water released from the WWTP (n = 2). Two ST235 isolates produced either the MBL IMP-29 (see above) or the ESBL PER-1. ST235 clones producing PER-1 have spread worldwide and have also been identified at our hospital [11]. CC111 includes isolates from ST111 and ST966 (Figures 3 and 4). Resistant CC111 isolates were isolated from both hospital wastewater (n = 3) and from treated water from the WWTP (n = 1). Finally, we found eight ST395 isolates at various points in the network: in hospital (n = 1) and urban (n = 2) wastewater, in untreated water from the WWTP (n = 2) and in the river downstream from the WWTP (n = 3). We previously showed that the widespread ST235, ST111 and ST395 were overrepresented among clinical AR-PA isolates in eastern France [11]. Moreover, a major outbreak involving more than 200 patients in our hospital between 1997 and 2009 was due to a ST395 clone with variable antibiotic resistance, as described in a previous study [30]. We therefore assume that the antibiotic-resistant isolates from ST235, CC111 and ST395 were probably released into the wastewater network by the hospital.

Surprisingly, we retrieved an unexpectedly high proportion of multidrug-resistant P. aeruginosa isolates from the river upstream from the WWTP (Figure 2). As hospitals are a major source of multidrug-resistant strains, we speculate that these multidrug-resistant P. aeruginosa probably came from the discharge, along the length of the river, from other plants treating wastewater from medical facilities. For example, there is a 1200-bed hospital located 80 km upstream. These data suggest that antibiotic-resistant bacteria may be maintained in the river water. Other studies have found traces of antibiotics (e.g. amoxicillin, sulfamethoxazole and fluoroquinolones) in French rivers [31], [32] that might contribute to the maintenance of resistant population in this environment [33].


We show here that P. aeruginosa is ubiquitous in the water network and that antibiotic-resistant (and, in particular, multidrug-resistant) strains are released from hospitals. Water treatment is effective at removing P. aeruginosa from the effluent, but does not decrease the proportion of antibiotic-resistant strains. Treated water and sewage sludge may therefore constitute a risk of environmental contamination with AR-PA released by hospitals.

Supporting Information

Table S1.

Sequence type, PFGE pattern, resistance profile and site of isolation of the P. aeruginosa isolates.



We thank Christian Imperas, Laurent Coty, Frédéric Pothin and the staff of the water supply facilities and wastewater treatment plant of the city of Besançon, France. We are also grateful to Emeline Muller from the Centre National de Référence de la Résistance aux Antibiotiques (Pr Patrick Plésiat) for the β-lactamase identification.

Author Contributions

Conceived and designed the experiments: CS DT XB DH. Performed the experiments: CS JP PC. Analyzed the data: CS MT XB DH. Wrote the paper: CS XB DT DH.


  1. 1. BMR-Raisin network (2010) Multidrug-resistant bacteria survey in French medical facilities: 2008 results.: Avalaible: Accessed 17 July 2012.
  2. 2. Normark S (1995) β-Lactamase induction in gram-negative bacteria is intimately linked to peptidoglycan recycling. Microb Drug Resist 1: 111–114.
  3. 3. Liao X, Hancock RE (1995) Cloning and characterization of the Pseudomonas aeruginosa pbpB gene encoding penicillin-binding protein 3. Antimicrob Agents Chemother 39: 1871–1874.
  4. 4. Khodursky AB, Cozzarelli NR (1998) The mechanism of inhibition of topoisomerase IV by quinolone antibacterials. J Biol Chem 273: 27668–27677.
  5. 5. Yoshida H, Nakamura M, Bogaki M, Nakamura S (1990) Proportion of DNA gyrase mutants among quinolone-resistant strains of Pseudomonas aeruginosa. Antimicrob Agents Chemother 34: 1273–1275.
  6. 6. Vettoretti L, Floret N, Hocquet D, Dehecq B, Plésiat P, et al. (2009) Emergence of extensive-drug-resistant Pseudomonas aeruginosa in a French university hospital. Eur J Clin Microbiol Infect Dis 28: 1217–1222.
  7. 7. Mesaros N, Nordmann P, Plésiat P, Roussel-Delvallez M, Van Eldere J, et al. (2007) Pseudomonas aeruginosa: resistance and therapeutic options at the turn of the new millennium. Clin Microbiol Infect 13: 560–578.
  8. 8. Strateva T, Yordanov D (2009) Pseudomonas aeruginosa - a phenomenon of bacterial resistance. J Med Microbiol 58: 1133–1148.
  9. 9. Kerr KG, Snelling AM (2009) Pseudomonas aeruginosa: a formidable and ever-present adversary. J Hosp Infect 73: 338–344.
  10. 10. Hocquet D, Berthelot P, Roussel-Delvallez M, Favre R, Jeannot K, et al. (2007) Pseudomonas aeruginosa may accumulate drug resistance mechanisms without losing its ability to cause bloodstream infections. Antimicrob Agents Chemother 51: 3531–3536.
  11. 11. Cholley P, Thouverez M, Hocquet D, van der Mee-Marquet N, Talon D, et al. (2011) Most multidrug-resistant Pseudomonas aeruginosa isolates from hospitals in eastern France belong to a few clonal types. J Clin Microbiol 49: 2578–2583.
  12. 12. Schwartz T, Volkmann H, Kirchen S, Kohnen W, Schön-Hölz K, et al. (2006) Real-time PCR detection of Pseudomonas aeruginosa in clinical and municipal wastewater and genotyping of the ciprofloxacin-resistant isolates. FEMS Microbiol Ecol 57: 158–167.
  13. 13. Antibiogram Committee of the French Society for Microbiology (2012) 2012 guidelines. Available: http://wwwsfm-microbiologieorg Accessed 17 July 2012.
  14. 14. Hocquet D, Dehecq B, Bertrand X, Plésiat P (2011) Strain-tailored double-disk synergy test detects extended-spectrum oxacillinases in Pseudomonas aeruginosa. J Clin Microbiol 49: 2262–2265.
  15. 15. Hocquet D, Plésiat P, Dehecq B, Mariotte P, Talon D, et al. (2010) Nationwide investigation of extended-spectrum β-lactamases, metallo- β-lactamases and extended-spectrum oxacillinases produced by ceftazidime-resistant Pseudomonas aeruginosa in France. Antimicrob Agents Chemother 54: 3512–3515.
  16. 16. Talon D, Cailleaux V, Thouverez M, Michel-Briand Y (1996) Discriminatory power and usefulness of pulsed-field gel electrophoresis in epidemiological studies of Pseudomonas aeruginosa. J Hosp Infect 32: 135–145.
  17. 17. Tenover FC, Arbeit RD, Goering RV, Mickelsen PA, Murray BE, et al. (1995) Interpreting chromosomal DNA restriction patterns produced by pulsed-field gel electrophoresis: criteria for bacterial strain typing. J Clin Microbiol 33: 2233–2239.
  18. 18. Curran B, Jonas D, Grundmann H, Pitt T, Dowson CG (2004) Development of a multilocus sequence typing scheme for the opportunistic pathogen Pseudomonas aeruginosa. J Clin Microbiol 42: 5644–5649.
  19. 19. van Mansfeld R, Willems R, Brimicombe R, Heijerman H, van Berkhout FT, et al. (2009) Pseudomonas aeruginosa genotype prevalence in Dutch cystic fibrosis patients and age dependency of colonization by various P. aeruginosa sequence types. J Clin Microbiol 47: 4096–4101.
  20. 20. Schouls LM, van der Heide HG, Vauterin L, Vauterin P, Mooi FR (2004) Multiple-locus variable-number tandem repeat analysis of Dutch Bordetella pertussis strains reveals rapid genetic changes with clonal expansion during the late 1990s. J Bacteriol 186: 5496–5505.
  21. 21. Maatallah M, Cheriaa J, Backhrouf A, Iversen A, Grundmann H, et al. (2011) Population structure of Pseudomonas aeruginosa from five Mediterranean countries: evidence for frequent recombination and epidemic occurrence of CC235. PLoS One 6: e25617.
  22. 22. Jeannot K, Poirel L, Robert-Nicoud M, Cholley P, Nordmann P, et al. (2012) IMP-29, a novel IMP-type metallo- β-lactamase in Pseudomonas aeruginosa. Antimicrob Agents Chemother 56: 2187–2190.
  23. 23. Mach PA, Grimes DJ (1982) R-plasmid transfer in a wastewater treatment plant. Appl Environ Microbiol 44: 1395–1403.
  24. 24. Quinteira S, Peixe L (2006) Multiniche screening reveals the clinically relevant metallo- β-lactamase VIM-2 in Pseudomonas aeruginosa far from the hospital setting: an ongoing dispersion process? Appl Environ Microbiol 72: 3743–3745.
  25. 25. Scotta C, Juan C, Cabot G, Oliver A, Lalucat J, et al. (2011) Environmental microbiota represents a natural reservoir for dissemination of clinically relevant metallo- β-lactamases. Antimicrob Agents Chemother 55: 5376–5379.
  26. 26. Tuméo E, Gbaguidi-Haoré H, Patry I, Bertrand X, Thouverez M, et al. (2008) Are antibiotic-resistant Pseudomonas aeruginosa isolated from hospitalised patients recovered in the hospital effluents? Int J Hyg Environ Health 211: 200–204.
  27. 27. Prado T, Pereira WC, Silva DM, Seki LM, Carvalho AP, et al. (2008) Detection of extended-spectrum β-lactamase-producing Klebsiella pneumoniae in effluents and sludge of a hospital sewage treatment plant. Lett Appl Microbiol 46: 136–141.
  28. 28. Yang CM, Lin MF, Liao PC, Yeh HW, Chang BV, et al. (2009) Comparison of antimicrobial resistance patterns between clinical and sewage isolates in a regional hospital in Taiwan. Lett Appl Microbiol 48: 560–565.
  29. 29. Morita Y, Murata T, Mima T, Shiota S, Kuroda T, et al. (2003) Induction of mexCD-oprJ operon for a multidrug efflux pump by disinfectants in wild-type Pseudomonas aeruginosa PAO1. J Antimicrob Chemother 51: 991–994.
  30. 30. Hocquet D, Bertrand X, Köhler T, Talon D, Plésiat P (2003) Genetic and phenotypic variations of a resistant Pseudomonas aeruginosa epidemic clone. Antimicrob Agents Chemother 47: 1887–1894.
  31. 31. Tuc Dinh Q, Alliot F, Moreau-Guigon E, Eurin J, Chevreuil M, et al. (2011) Measurement of trace levels of antibiotics in river water using on-line enrichment and triple-quadrupole LC–MS/MS. Talanta 85: 1238–1245.
  32. 32. Tamtam F, Mercier F, Eurin J, Chevreuil M, Le Bot B (2009) Ultra performance liquid chromatography tandem mass spectrometry performance evaluation for analysis of antibiotics in natural waters. Anal Bioanal Chem 393: 1709–1718.
  33. 33. Gullberg E, Cao S, Berg OG, Ilback C, Sandegren L, et al. (2011) Selection of resistant bacteria at very low antibiotic concentrations. PLoS Pathog 7: e1002158.