Research Article | Open Access
Occurrence of β-Lactamase-Producing Gram-Negative Bacterial Isolates in Water Sources in Cali City, Colombia
Introduction. Pollution by domestic, industrial, and hospital wastes of the artificial and natural waters of the city of Cali led us to investigate the presence of Gram-negative bacteria resistant to antibiotics in these aquatic ecosystems. Material and methods. We used culture-dependent methods and molecular techniques to investigate the prevalence and dynamics of β-lactamase producing Gram-negative bacteria in five areas located in channels and rivers that cross the city of Cali in January (dry season) and May (wet season). The association between the variables was determined by the chi-square test, using the statistical package SPSS vs 23.0. Results. The main species being Escherichia coli and Pseudomonas spp. with associated resistance to both cefoxitin and cefotaxime were observed in 73.3% isolates during the dry season. Most of the isolates belonged to antibiotype 3 (with resistance to 6 antibiotics), 51.2% in the dry season and 48.9% in the wet season, and they were found especially in the artificial waters of “Intersector Canal (CVC) Sur”. Conclusion. These results indicate that β-lactamase-producing Gram-negative bacteria are widespread in the environment in the aquatic ecosystem of Cali city. The artificial and natural waters that cross the city are finally discharged into the Rio Cauca; this river can then be considered as a medium for the spread of bacterial antibiotic resistance genes.
Antibiotic-resistant bacteria and antibiotic resistance genes (ARGs) which are introduced into aquatic environments greatly affect public health since these environments are used for various purposes [1–5].
Resistant organisms and ARGs in aquatic environments can occur through contamination of these bodies of water with wastes that mainly contain remnants of antibiotics and direct input of antibiotic-resistant bacteria [6, 7]. The major source of antibiotic contamination in surface water comes from effluents from industries, hospitals, and domestic wastewater treatment plants [8–13]. In the case of antibiotic-resistant bacteria, human and animal waste and agricultural activities are the main causes of their introduction into the aquatic environment [1, 4, 6, 8, 13, 14].
ARGs may be horizontally or vertically transferred between communities of environmental bacteria [15–17]. Aquatic environments can act as a facilitator for the exchange of mobile elements responsible for resisting antibiotics.
In Gram-negative bacteria, the presence of β-lactamases is an important defense mechanism against the antibiotics of this group [22–24]. The first β-lactamases discovered were TEM-1, TEM-2, and SHV-1, later called broad-spectrum β-lactamases. The product of mutations of the genes that encode these enzymes gave rise to current extended-spectrum β-lactamases (ESBLs), CTX-M family (from chromosomal beta-lactamases of the Kluyvera genus), and other less prevalent, all of them included in the functional group 2be of Bush and Jacoby . Since its initial description, more than 300 different ESBLs have been identified, and the majority belongs to the TEM, SHV, and CTX-M families (https://www.ncbi.nlm.nih.gov/pathogens/beta-lactamase-data-resources/). These enzymes are encoded in plasmids and are transferable to other bacteria by conjugation, which has favored their rapid dispersion.
In recent years, the presence of Gram-negative bacilli resistant to carbapenems has been reported due to the production of β-lactamases capable of hydrolyzing this group of antimicrobials.
Some publications mention the relevance of four types of enzymes that are becoming important in new clinical isolates and in resistance in Gram-negative bacteria. These are extended-spectrum β-lactamases (ESBLs), β-lactamases with reduced sensitivity to β-lactamase inhibitors, plasmid-mediated β-lactamase AmpC, and β-lactamases that hydrolyze carbapenems (belonging to the groups C, A and D, and A and B of the Ambler classification (1) or to groups 1, 2 and 2be, and 3a, 3b, and 3c of the Bush classification) [25, 26].
In Colombia, the presence of β-lactamases in members of the family Enterobacteriaceae and nonfermenting Gram-negative bacilli is reported very frequently. Surveillance studies of resistance are carried out mainly in the hospital environment [31–33]. However, there is little information on the identity and distribution of resistance genes in bacterial isolates in other environments. In this study, we report the prevalence of β-lactam antibiotic resistance in Gram-negative bacilli isolated from the artificial and natural waters of the city of Cali and the distribution of genetic elements that may be responsible for the observed antibiotic resistance.
2. Material and Methods
2.1. Study Area and Sampling
The study site is located in Cali city, at coordinates 3° 27′00 ″N 76° 32′00″ W, in southwestern Colombia. It is the third most populated city in Colombia. The main river of the city is the Cauca River, which halfway through the city receives the pollutant load of the so-called “Intersector Canal (CVC) Sur” (sampling site C), which mobilizes the wastewater from the southeast of the city. Following the course of the Cauca River, 11 km downstream is the water treatment plant “Puerto Mallarino” (sampling site D) that supplies 80% of the water consumed by the city. 3.4 km later, there is the wastewater treatment plant “Cañaveralejo PTAR-C” (sampling site A). The city also has the Cañaveralejo and Melendez rivers (sampling site E) that originate in the center of the city and end at the southern CVC Intersector channel.
In January (dry season) and May (wet season) of 2017, three samples per location were collected from five areas at the points indicated on the map (Figure 1).
Wastewater effluent and incoming river water samples were collected by point collection in triplicate in 500 ml brown glass bottles protected with an aluminum seal and/or a Teflon cap, completely filled, and kept at 4°C in an icebox containing ice during transportation to the laboratory and processed immediately for the enumeration of bacteria.
2.2. Bacterial Counts, Isolation, and Identification
Viable counts in wastewater effluent and river water samples were estimated by preparing serial ten-fold dilutions from 10–1 to 10–6. A standard volume of each dilution was then inoculated on duplicate plates of CHROMagar total coliforms (CHROMagar™ ECC, DRG International Inc.) to determine coliform counts. After incubation at 37°C for 48 hours, colonies of coliform bacilli were counted.
Water samples were diluted 1 : 1 in 0.85% saline solution prior to inoculation. After overnight incubation, the broth was subcultured onto MacConkey agar (Oxoid Ltd., Hampshire, United Kingdom) to isolate and identify the selected Gram-negative enteric bacteria and cetrimide agar (Merck, Germany) to isolate Pseudomonas spp. Bacterial identification was confirmed using the Vitek GNI + card (bioMerieux Vitek Inc., Hazelwood, MO). Pure strains with no more than 24 hours of growth were used and a 1.0 McFarland suspension was prepared in saline solution, which was used to inoculate the Vitek cards at a fixed incubation temperature of 37°C following the manufacturer’s instructions. The Vitek system is an automated system that is based on the inoculation of a suspension of microorganisms on cards with certain biochemical reactions panels and allows species-level identification of Gram-negative bacilli.
A total of 80 (31 of E. coli, 25 of Klebsiella spp., and 24 of Pseudomonas spp.) and 86 (42 of E. coli, 16 of Klebsiella spp., and 28 of Pseudomonas spp.) isolates were selected from the water samples in the dry season and wet season, respectively.
2.3. Determination of Antibiotic Resistance Profiles
Antibiotic resistance profiles were obtained from 166 isolates. A standardized amount was inoculated (standard 0.5 of McFarland) and antimicrobial susceptibility testing was performed by the disk diffusion method on Mueller–Hinton (MH) agar (Difco Laboratories, Detroit, MI, USA) using interpretative criteria of the Clinical and Laboratory Standard Institute (CLSI) . The following antimicrobials were used: trimethoprim/sulfametoxazol (SXT, 23.75 μg + 1.25 μg), gentamicin (GEN, 10 μg), ciprofloxacin (CIP, 5 μg), ceftazidime (CAZ, 30 μg), cefoxitin (FOX, 30 μg), cefotaxime (CTX, 30 μg), meropenem (MEM, 10 μg), piperacillin/tazobactam (TZP, 40 μg), and cefixime (CFM, 5 μg) (Oxoid Ltd., Hampshire, United Kingdom). ESBL-positive isolates were identified by using the double-disk synergy test with third-generation cephalosporins (cefotaxime, ceftazidime, and cefixime) alone and with clavulanic acid. Quality control was carried out using standard strains of Escherichia coli (ATCC 25922) and Pseudomonas aeruginosa (ATCC 27953). Intermediate susceptibility to each antibiotic was considered to be resistant.
According to the definitions proposed by Magiorakos et al., resistance to three or more antibiotic classes was defined as multidrug resistant (MDR) .
2.4. DNA Extraction and Quantification
DNA extraction was carried out from a bacterial culture in LB (Luria–Bertani) broth at 37°C overnight using a genomic DNA extraction kit (MO BIO Laboratories Inc.).
The concentration of DNA in the samples was quantified by using a FOTO/Analyst® Investigator/FX Systems (FOTODYNE Incorporated).
2.5. Polymerase Chain Reaction (PCR) to Detect bla Genes
Amplification was carried out in 50 μl volumes with 5–10 ng (genomic DNA) reaction buffer, 1 U of Taq polymerase (Bioline, London, United Kingdom), 200 μM deoxynucleoside triphosphate, 1.5 or 2.5 mM MgCl2, 10 pmol of each primer, and 4 μl of DNA as the template. PCR conditions generally were as follows: a hot start at 94°C for 5 min; 35 cycles of either 30 s at 94°C, 45 s at 52°C (blaTEM-1), 45 s at 51°C (blaCXT-M-9 and blaAmpC), 1 min at 51°C (blaVIM-2 and blaIMP-1), or 60 s at 72°C; and a final step of 10 min at 72°C.
The amplified DNA products were analyzed by conventional 1.5% (wt/vol) agarose gel electrophoresis in 1X TAE buffer and run at 100 V for 1 h. To visualize band migration, the gel was stained with ethidium bromide and observed under UV light. A 100-bp or 1-kb ladder (Gibco BRL, Ontario) was used to estimate the amplicon size.
2.6. Statistical Methods
Differences in frequencies of β-lactamase genotypes among groups were evaluated using chi-square tests (χ2) using contingency tables with a significance level of . Univariate analysis of variance was performed for inference on differences in the average numbers of multidrug resistance between β-lactamase genotypes. Analyses were performed in IBM SPSS Statistics version 23.0 (SPSS Inc., Chicago).
This study recorded total coliform counts ranging from 2.32 × 105 CFU/ml to 4.57 × 105 CFU/ml in the dry season and 6.6 × 103 CFU/ml to 2 × 104 CFU/ml in the wet season. A variety of organisms such as Pseudomonas spp., Acinetobacter spp., Pasteurella spp., Aeromonas spp., Proteus spp., Klebsiella spp., Enterobacter spp., Alcaligenes spp., and Escherichia coli comprised the majority of the isolates.
However, to carry out specific studies on susceptibility to antibiotics and detection of resistance genes, only isolates of E. coli, K. pneumoniae, and Pseudomonas spp. were used, since they are the most abundant, in the amounts indicated in Material and Methods.
3.1. Antimicrobial Susceptibility
Isolates were subjected to an antibiotic susceptibility test using 8 different antibiotics from which their antibiotic resistance profiles and multiple antibiotic resistance phenotypes were compiled from the five areas. The results obtained are depicted in Table 2 and revealed that a large proportion of the environmental isolates was resistant to cefoxitin and meropenem (78.8%) during the wet season, followed by ciprofloxacin. During the dry season, resistance to cefoxitin and cefotaxime reached 73.2% followed by resistance to piperacillin/tazobactam (72%).
Trimetroprim/sulfametoxazol (SXT), gentamicin (GEN), ciprofloxacin (CIP), ceftazidime (CAZ), cefoxitin (FOX), cefotaxime (CTX), meropenem (MEM), piperacillin/tazobactam (TZP); wastewater treatment plant (A), rainwater channel (B), Intersector Canal (CVC) Sur (C), water treatment plant “Puerto Mallarino” (D), and Melendez River (E). DS: dry season, WS: wet season. .
Ninety-six and a half percentage (96.5%) of the isolates were resistant to >1 antibiotics during the wet season, while 47.7% of the isolates were resistant to 2 or more classes of antibiotics tested during the dry season. The rates of resistance were highest during the wet season (96.6%), and during the dry season, the resistance was lower (75.7%).
All isolates obtained during the dry and wet seasons were grouped into four (1 to 4) different antibiotypes depending on their susceptibilities to 8 different antimicrobial drugs (Table 3). MDR (3 to 8 antibiotics) bacteria were common among the isolates, and these corresponded to the isolates of antibiotypes 1, 2 and 3.
Trimetroprim/sulfametoxazol (SXT), gentamicin (GEN), ciprofloxacin (CIP), ceftazidime (CAZ), cefoxitin (FOX), cefotaxime (CTX), meropenem (MEM), piperacillin/tazobactam (TZP); wastewater treatment plant (A), rainwater channel (B), Intersector Canal (CVC) Sur (C), water treatment plant “Puerto Mallarino” (D), and Melendez River (E). DS: dry season, WS: wet season; Ant: antibiotype.
Interestingly, antibiotypes were grouped significantly in the sites tested during the wet season (). Most isolates belonged to antibiotype 3 (51.2% in the dry season and 48.9% in the wet season) and were found especially at the site called “Intersector Canal (CVC) Sur”.
In some cases, the isolates were resistant to up to eight different antibiotics and correspond to antibiotype 1; most of these isolates were found at the rainwater channel (23.1% in the dry season and 27.3% in the wet season).
Antibiotype 4 with isolates showed sensitivity to all the antibiotics tested and represented 22% during the dry season but decreased to 3.4% during the wet season (only determined at the site called “Intersector Canal (CVC) Sur”, 10%).
Table 4 shows that the presence of carbapenemases was more common (36.1%) and was detected in 50% of the isolates from the artificial waters of Intersector Canal (CVC) Sur during the wet season, similarly to the ESBL. However, all ESBL isolates showed a lower prevalence (27.1%).
Wastewater treatment plant (A), rainwater channel (B), Canal Sur (C), water treatment plant “Puerto Mallarino” (D), and Melendez River (E). DS: dry season, WS: wet season. blaTEM-1 and 0.024ψ; blaCTXM-9; blaAmpC and 0.008ψ; blaIMP-1; blaVIMP-2.
Isolates with AmpC were found in 16.7% and isolates with broad-spectrum β-lactamases represented 10.8%, even though they were not detected during the wet season in the channel of rainwater.
3.2. bla Genes Present in Isolates
We found that 75% and 88.4% of all the isolates identified had at least one type of gene bla in the dry and wet seasons, respectively. Of these, 31.3% and 36% were positive for two or more genes, respectively.
The rainwater channel and Intersector Canal (CVC) Sur showed the highest number of isolates with bla genes in 75.6% and 40.7%, respectively. These two sites receive artificial water, consisting mainly of domestic and industrial wastewater from the city of Cali, and in the Cauca River, which collects all the artificial and natural waters of the city, the number of isolates with bla genes reached up to 24.4% during the wet season.
DNA from a total of 166 isolates was amplified; 82 (49.4%) isolates were identified as containing blaVIM-2, 75 (45.2%) were identified as containing blaTEM-1, 38 (22.9%) strains contained blaIMP-1, 34 (20.5%) strains contained blaAmpC, 24 (14.5%) strains contained blaCTXM-9, and 28 (16.9%) did not amplify (Table 4).
The contamination of artificial and natural surface waters with pathogenic bacteria is a major problem for developed countries and developing countries such as Colombia .
We used culture-dependent methods to investigate the prevalence and dynamics of heterotrophic antibiotic-resistant bacteria from natural (water treatment plant “Puerto Mallarino” and Melendez River) and artificial (wastewater treatment plant, rainwater channel, and Intersector Canal (CVC) Sur) water sources. The group of total coliforms comprises a wide range of microorganisms that are found everywhere in aqueous and soil environments; they develop very well in the intestinal tract of humans and mammals (fecal coliforms), as well as in the organic material originated by the decaying vegetation.
Although the natural mortality of coliform populations is very high, especially in fecal coliforms due to adverse conditions in the extraenteric environment, their great abundance could be evidenced during the dry season, reaching orders of 105 CFU/ml, which is in accordance with the reports of McFeters, who reported values of 105–1010 CFU/ml of total coliforms in wastewater . Certain environmental conditions (turbidity, temperature, etc.) can keep these populations viable for a long time [42, 43].
However, the amount of the coliform population decreased to an order of 103 CFU/ml during the wet season. The reason for this difference could be the reduction of the flow in the rivers during the dry season, which is maintained mainly by the artificial domestic, hospital, and industrial wastewater which would be the main sources of these bacteria.
Davino et al.  and Delgado et al. , analyzing the coliform counts in Jatiúca Beach, Brazil, and Bassaseachic Falls National Park, Mexico, respectively, reported that the fecal coliform count was higher during the wet seasons (May, June, and July) than during the dry seasons (November, December, and January), indicating water movement during higher temperatures [44–46].
The presence and persistence of bacteria resistant to antibiotics have been described in surface water, representing a growing public health problem [42–48]. The data collected in the present work allow us to affirm that in the city of Cali, the same problematic situation is presented.
Water samples collected during the sampling period present a pattern of resistance to antibiotics against dispar. The highest number of resistant isolates was obtained significantly to third-generation cephalosporins and β-lactamase inhibitors during the dry season, reaching values above 70%, especially in the artificial waters of the rainwater channel and in Intersector Canal (CVC) Sur. The resistance prevalence data of Gram-negative bacilli resistant to β-lactams were similar to those detected in the sewage system of the city of Rio de Janeiro  and other cities in Brazil . These antibiotics are the most used in the treatment of infections caused by Gram-negative bacilli, which shows the selective pressure that is exerted on bacteria of fecal and natural origin.
In relation to the susceptibility profiles, no statistically significant differences were found between the samples of artificial and natural waters. However, a MDR profile (especially, antibiotype 3) with resistance to more than 6 antibiotics was the most prevalent in the sampling sites. In accordance with the results of the study of Chelosi et al.  more than 56% of Gram-negative bacteria from cultured marine sediments in western Mediterranean were found to have resistance to 5 or more antibiotics.
In addition, the percentages of MDR bacteria to antibiotics obtained in this study correspond to the ranges of resistance found by other authors. Thus, MDR isolates from the Enterobacteriaceae family have been identified in Bassaseachic Falls National Park, Mexico , and in the Almendares River in Cuba .
Reports indicate that the frequency of MDR organisms varies according to the environment and period and shows an increasing number of these phenotypes in natural environments [9, 19, 30, 39, 43, 46, 47].
A further objective of this study was to characterize β-lactamase-producing Gram-negative bacteria; individual isolates of β-lactamase-producing bacteria were found during the dry season (24.4%) and wet season (34.5%). In concordance with these results, the prevalence of Gram-negative bacteria in the aquatic environment has been already reported, especially those of the coliform group. More than 50% of the diseases caused by contaminated water are associated with bacteria from the intestinal microbiota, such as Enterobacteriaceae and the coliform group [21, 28, 29]. The contamination of these environments reflects the poor quality, hygiene, and sanitization of the water [1–7].
In this study, we detected carbapenemases, ESBLs, broad-spectrum β-lactamases, and inducible chromosomal β-lactamases. The largest number of isolates with β-lactamases was concentrated in the waters of Intersector Canal (CVC) Sur. This channel collects domestic, hospital, and industrial wastewater from a large part of the city and mixes it with the natural waters of the Melendez and Cañaveralejo rivers to finally be discharged into the Cauca River (the second largest river in Colombia). This situation is repeated in many of the rivers that cross the main Colombian cities. The excessive use of β-lactam antibiotics and their inadequate disposition are factors that promote the appearance of resistant organisms in the environment, so their proper use would be an appropriate measure to preserve this powerful family of antibiotics.
Bacteria may inherit resistance to some antibiotics or can develop resistance via spontaneous mutation or the acquisition of resistant genes [14–17]. The resistance in Gram-negative bacteria to β-lactam antibiotics is largely due to the acquisition of bla genes, which code for a broad group of β-lactamases.
We found more than 75% of isolates with bla genes during the dry and wet seasons, mainly in artificial waters. blaTEM-1, blaCTX-M-9, blaVIM-2, blaIMP-1, and blaAmpC genes were detected in almost all samples of artificial and natural waters, which shows that these genes are widely distributed in the city’s water systems. The finding of this high percentage of bla genes in environmental isolates reveals the selective antibiotic pressure that would be exerted on them and/or the dissemination of resistance genes among bacterial populations of water systems.
One limitation of this study was only the identification of the blaCTX-M-9 gene; although together with the CTX-M-14 enzyme, it is frequently found in Latin American countries, and the identification of CTX-M-15 (CTX-M-1 group) would have been useful because of its wide global distribution .
The study shows that the artificial and natural waters of the city are contaminated with resistant bacteria and can contribute to the spread of these bacteria.
Isolates with resistance to β-lactam antibiotics, especially third-generation cephalosporins, were more prevalent during the dry season. However, there was no statistically significant variation from data found in the wet season.
The presence of Gram-negative bacteria resistant to more than 6 antibiotics (represented by antibiotypes 1 and 3) was evidenced in the natural and artificial waters of the city, representing a risk to humans and the environment in that they can act as reservoirs of resistant bacteria and contributing to the storage and diffusion of antibiotic resistance genes.
We also found isolates with resistance to non-β-lactam antibiotics showing that these isolates have developed more than one mechanism of resistance. This suggests that these strains have been subjected to multiple selective pressures upon being in the constant presence of antibiotics, thus causing them to become resistant to higher order drugs.
The artificial and natural waters that cross the city of Cali are finally discharged into the Rio Cauca, and this river can then be considered (a) as a medium for the spread of bacterial antibiotic resistance genes, (b) acts as a reservoir for these genes and (c) due to socio-economic pressure, may play a role in the development and evolution of these genes along this river system.
All the data used in this study are included within the article.
Conflicts of Interest
The authors declare that they have no conflicts of interest.
The authors thank the General Research Direction (DGI) at the Universidad Santiago de Cali for the economic support to conduct this study.
- C. Xi, Y. Zhang, C. F. Marrs et al., “Prevalence of antibiotic resistance in drinking water treatment and distribution systems,” Applied and Environmental Microbiology, vol. 75, no. 17, pp. 5714–5718, 2009.
- S. Khan, C. W. Knapp, and T. K. Beattie, “Antibiotic resistant bacteria found in municipal drinking water,” Environmental Processes, vol. 3, no. 3, pp. 541–552, 2016.
- C. Ding and J. He, “Effect of antibiotics in the environment on microbial populations,” Applied Microbiology and Biotechnology, vol. 87, no. 3, pp. 925–941, 2010.
- M. Williams, R. Stedtfeld, X. Guo et al., “Antimicrobial resistance in the environment,” Water Environment Research, vol. 88, no. 10, pp. 1951–1967, 2016.
- C. L. Ventola, “The antibiotic resistance crisis: part 1: causes and threats,” Pharmacology & Therapeutics, vol. 40, no. 4, pp. 277–283, 2015.
- C. Seiler and T. U. Berendonk, “Heavy metal driven co-selection of antibiotic resistance in soil and water bodies impacted by agriculture and aquaculture,” Frontiers in Microbiology, vol. 3, p. 399, 2012.
- V. V. Martins, M. O. B. Zanetti, A. Pitondo-Silva, and E. G. Stehling, “Aquatic environments polluted with antibiotics and heavy metals: a human health hazard,” Environmental Science and Pollution Research, vol. 21, no. 9, pp. 5873–5878, 2014.
- F. C. Cabello, H. P. Godfrey, A. Tomova et al., “Antimicrobial use in aquaculture re-examined: its relevance to antimicrobial resistance and to animal and human health,” Environmental Microbiology, vol. 15, no. 7, pp. 1917–1942, 2013.
- H. Chen and M. Zhang, “Occurrence and removal of antibiotic resistance genes in municipal wastewater and rural domestic sewage treatment systems in eastern China,” Environment International, vol. 55, pp. 9–14, 2013.
- F. Marinescu and V. Lazar, “Origins, transfer and accumulation of antibiotic resistance genes in the aquatic environment,” Biointerface Research in Applied Chemistry, vol. 3, no. 3, pp. 588–598, 2013.
- N. Devarajan, A. Laffite, P. Ngelikoto et al., “Hospital and urban effluent waters as a source of accumulation of toxic metals in the sediment receiving system of the Cauvery River, Tiruchirappalli, Tamil Nadu, India,” Environmental Science and Pollution Research, vol. 22, no. 17, pp. 12941–12950, 2015.
- K. Kümmerer, “The presence of pharmaceuticals in the environment due to human use—present knowledge and future challenges,” Journal of Environmental Management, vol. 90, no. 8, pp. 2354–2366, 2009.
- P. S. McManus, V. O. Stockwell, G. W. Sundin, and A. L. Jones, “Antibioticuse inplantagriculture,” Annual Review of Phytopathology, vol. 40, no. 1, pp. 443–465, 2002.
- T. U. Berendonk, C. M. Manaia, C. Merlin et al., “Tackling antibiotic resistance: the environmental framework,” Nature Reviews Microbiology, vol. 13, no. 5, pp. 310–317, 2015.
- X. Bellanger, H. Guilloteau, S. Bonot, and C. Merlin, “Demonstrating plasmid-based horizontal gene transfer in complex environmental matrices: a practical approach for a critical review,” Science of the Total Environment, vol. 493, pp. 872–882, 2014.
- J. Bengtsson-Palme and D. G. J. Larsson, “Antibiotic resistance genes in the environment: prioritizing risks,” Nature Reviews Microbiology, vol. 13, no. 6, p. 396, 2015.
- M. Brown-Jaque, W. Calero-Cáceres, and M. Muniesa, “Transfer of antibiotic-resistance genes via phage-related mobile elements,” Plasmid, vol. 79, pp. 1–7, 2015.
- D. A. Antonopoulos, S. M. Huse, H. G. Morrison, T. M. Schmidt, M. L. Sogin, and V. B. Young, “Reproducible community dynamics of the gastrointestinal microbiota following antibiotic perturbation,” Infection and Immunity, vol. 77, no. 6, pp. 2367–2375, 2009.
- S. Papandreou, O. Pagonopoulou, A. Vantarakis, and M. Papapetropoulou, “Multiantibiotic resistance of Gram-negative bacteria isolated from drinking water samples in southwest Greece,” Journal of Chemotherapy, vol. 12, no. 4, pp. 267–273, 2000.
- D. M. McKeon, J. P. Calabrese, and G. K. Bissonnette, “Antibiotic resistant Gram-negative bacteria in rural groundwater supplies,” Water Research, vol. 29, no. 8, pp. 1902–1908, 1995.
- E. M. Wellington, A. B. Boxall, P. Cross et al., “The role of the natural environment in the emergence of antibiotic resistance in Gram-negative bacteria,” The Lancet Infectious Diseases, vol. 13, no. 2, pp. 155–165, 2013.
- D. Rawat and D. Nair, “Extended-spectrum β-lactamases in Gram negative bacteria,” Journal of Global Infectious Diseases, vol. 2, no. 3, pp. 263–274, 2010.
- C. C. Sanders and W. E. Sanders Jr., “Type I-lactamases of Gram-negative bacteria: interactions with-lactam antibiotics,” Journal of Infectious Diseases, vol. 154, no. 5, pp. 792–800, 1986.
- É. Ruppé, P. L. Woerther, and F. Barbier, “Mechanisms of antimicrobial resistance in Gram-negative bacilli,” Annal of Intensive Care, vol. 5, p. 21, 2015.
- K. Bush, G. A. Jacoby, and A. A. Medeiros, “A functional classification scheme for beta-lactamases and its correlation with molecular structure,” Antimicrobial Agents and Chemotherapy, vol. 39, no. 6, pp. 1211–1233, 1995.
- K. S. Thomson and E. S. Moland, “Version 2000: the new β-lactamases of Gram-negative bacteria at the dawn of the new millennium,” Microbes and Infection, vol. 2, no. 10, pp. 1225–1235, 2000.
- E. Marti, E. Variatza, J. L. Balcazar et al., “The role of aquatic ecosystems as reservoirs of antibiotic resistance,” Trends in Microbiology, vol. 22, no. 1, pp. 36–41, 2014.
- C. Brechet, J. Plantin, M. Sauget et al., “Wastewater treatment plants release large amounts of extended-spectrum β-lactamase-producing Escherichia coli into the environment,” Clinical Infectious Diseases, vol. 58, no. 12, pp. 1658–1665, 2014.
- E. Ojer-Usoz, D. González, I. García-Jalón, and A. I. Vitas, “High dissemination of extended-spectrum β-lactamase-producing Enterobacteriaceae in effluents from wastewater treatment plants,” Water Research, vol. 56, pp. 37–47, 2014.
- K. Zurfluh, H. Hächler, M. Nüesch-Inderbinen, and R. Stephan, “Characteristics of extended-spectrum β-lactamase- and carbapenemase-producing Enterobacteriaceae isolates from rivers and lakes in switzerland,” Applied and Environmental Microbiology, vol. 79, no. 9, pp. 3021–3026, 2013.
- E. Valenzuela, J. Mantilla, M. Reguero et al., “Detection of CTX-M-1, CTX-M-15, and CTX-M-2 in clinical isolates of enterobacteriaceae in bogotá, Colombia,” Journal Clinic of Microbiology, vol. 44, no. 5, pp. 1919-1920, 2005.
- P. Espinal, U. Garza-Ramos, F. Reyna et al., “Identification of SHV-Type and CTX-M-12 extended-spectrum β-lactamases (ESBLs) in multiresistant Enterobacteriaceae from Colombian caribbean hospitals,” Journal of Chemotherapy, vol. 22, no. 3, pp. 160–164, 2010.
- L. J. Rojas, M. F. Mojica, V. M. Blanco et al., “Emergence of Klebsiella pneumoniae coharboring KPC and VIM carbapenemases in Colombia,” Antimicrobial Agents and Chemotherapy, vol. 57, no. 2, pp. 1101-1102, 2013.
- Clinical and Laboratory Standards Institute, Performance Standards for Antimicrobial Susceptibility Testing; 25th Informational Supplement, CLSI M100-S25 Clinical and Laboratory Standards Institute, Wayne, PA, USA, 2015.
- A.-P. Magiorakos, A. Srinivasan, R. B. Carey et al., “Multidrug-resistant, extensively drug-resistant and pandrug-resistant bacteria: an international expert proposal for interim standard definitions for acquired resistance,” Clinical Microbiology and Infection, vol. 18, no. 3, pp. 268–281, 2012.
- C. Mabilat and P. Courvalin, “Development of “oligotyping” for characterization and molecular epidemiology of TEM beta-lactamases in members of the family Enterobacteriaceae,” Antimicrobial Agents and Chemotherapy, vol. 34, no. 11, pp. 2210–2216, 1990.
- L. Poirel, T. Naas, D. Nicolas et al., “Characterization of VIM-2, a carbapenem-hydrolyzing metallo-beta-lactamase and its plasmid-and integron-borne gene from a Pseudomonas aeruginosa clinical isolate in france,” Antimicrobial Agents and Chemotherapy, vol. 44, no. 4, pp. 891–897, 2000.
- A. D. Khosravi and F. Mihani, “Detection of metallo-β-lactamase-producing Pseudomonas aeruginosa strains isolated from burn patients in Ahwaz, Iran,” Diagnostic Microbiology and Infectious Disease, vol. 60, no. 1, pp. 125–128, 2008.
- P. E. Coudron, E. S. Moland, and K. S. Thomson, “Occurrence and detection of AmpC beta-lactamases among Escherichia coli, Klebsiella pneumoniae, and Proteus mirabilis isolates at a veterans medical center,” Journal of Clinical Microbiology, vol. 38, no. 5, pp. 1791–1796, 2000.
- B. L. Guzman, G. Nava, and P. D. Bevilacqua, “Surveillance of drinking water quality in Colombia: challenges for environmental health,” Revista Facultad Nacional de Salud Publica, vol. 34, no. 2, pp. 175–183, 2016.
- G. A. McFeters, Drinking Water Microbiology, Springer, Berlin, Germany, 1990.
- C. M. Davies and H. J. Bavor, “The fate of stormwater-associated bacteria in constructed wetland and water pollution control pond systems,” Journal of Applied Microbiology, vol. 89, no. 2, pp. 349–360, 2000.
- T. P. G. Chagas, L. M. Seki, J. C. Cury et al., “Multiresistance, beta-lactamase-encoding genes and bacterial diversity in hospital wastewater in Rio de Janeiro, Brazil,” Journal of Applied Microbiology, vol. 111, no. 3, pp. 572–581, 2011.
- A. M. C. Davino, M. B. D. Melo, and R. A. Caffaro Filho, “Assessing the sources of high fecal coliform levels at an urban tropical beach,” Brazilian Journal of Microbiology, vol. 46, no. 4, pp. 1019–1026, 2015.
- M. C. Delgado, P. Tamez, R. Gomez et al., “Multidrug-resistant bacteria isolated from surface water in bassaseachic falls national park, Mexico,” International Journal of Environmental Research and Public Health, vol. 13, no. 6, p. E597, 2016.
- J. A. Resende, V. L. Silva, C. Oliveira et al., “Multidrug-resistance and toxic metal tolerance of medically important bacteria isolated from an aquaculture system,” Microbes and Environments, vol. 27, no. 4, pp. 449–455, 2012.
- D. W. Graham, S. Olivares-Rieumont, C. W. Knapp, L. Lima, D. Werner, and E. Bowen, “Antibiotic resistance gene abundances associated with waste discharges to the almendares river near Havana, Cuba,” Environmental Science & Technology, vol. 45, no. 2, pp. 418–424, 2011.
- E. Chelossi, S. Vezzulli, L. Milano et al., “Antibiotic resistance of benthic bacteria in fish-farm and control sediments of the western mediterranean,” Aquaculture, vol. 219, no. 4, pp. 83–97, 2003.
- R. Cantón, J. M. González-Alba, and J. C. Galán, “CTX-M enzymes: origin and diffusion,” Frontiers in Microbiology, vol. 3, p. 110, 2012.
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