Genetic Characterization of Antimicrobial-Resistant Escherichia coli Isolated from a Mixed-Use Watershed in Northeast Georgia, USA

In order to determine the role of surface water in the development and spread of antibiotic-resistant (AR) bacteria, water samples were collected quarterly from 2015 to 2016 from a mixed-use watershed in Georgia. In our previous study, 496 Escherichia coli were isolated from surface water, out of which, 34 isolates were resistant to antimicrobials. For the current study, these 34 AR E. coli were characterized using pulsed-field gel electrophoresis, AR gene detection, plasmid replicon typing, class I integron detection, and multi-locus sequence typing. Genes were identified as conferring resistance to azithromycin (mph(A)); β-lactams (blaCMY, blaCTX, blaTEM); chloramphenicol (floR); streptomycin (strA, strB); sulfisoxazole (sul1, sul2); tetracycline (tetA, tetB, tetC); and trimethoprim/sulfamethoxazole (dhfr5, dhfr12). Five ciprofloxacin- and/or nalidixic-resistant isolates contained point mutations in gyrA and/or parC. Most of the isolates (n = 28) carried plasmids and three were positive for class I integrons. Twenty-nine sequence types (ST) were detected, including three epidemic urinary-tract-infection-associated ST131 isolates. One of the ST131 E. coli isolates exhibited an extended-spectrum β-lactamase (ESBL) phenotype and carried blaCTX-M-15 and blaTEM-1. To our knowledge, this is the first study on the emergence of an ESBL-producing E. coli ST131 from environmental water in the USA, which poses a potential risk to human health through the recreational, agricultural, or municipal use of this natural resource. This study identified E. coli with AR mechanisms to commonly used antimicrobials and carrying mobile genetic elements, which could transfer AR genes to other bacteria in the aquatic environment.


Introduction
Antibiotic-resistant (AR) pathogens are a significant public health concern as infections caused by these pathogens may result in prolonged hospital stays, higher medical costs, and increased rates of morbidity and mortality [1]. Although Escherichia coli are usually commensal bacteria in the gastrointestinal tract of humans and animals, they can cause intestinal and extra-intestinal infections, such as gastroenteritis, urinary tract infection, meningitis, and sepsis [2]. Since E. coli can readily acquire resistance and are shown to carry resistance to antimicrobial drugs used in human and veterinary medicine, the monitoring of AR E. coli in all settings is necessary to understand their impact associated with AR E. coli infections [1,2].
There is a growing recognition of the environment as an important factor in the emergence, transmission, and persistence of AR bacteria in light of the One Health perspective, which accepts that the health of humans, animals, and the environment are closely related [3]. The aquatic environment is a hotspot for the development of AR bacteria. Surface and sub-surface waters receive bacteria harboring AR genes from human and animal wastes, as well as antibiotic residues from healthcare, industrial, and agricultural activities. Surface water can also be a vector for the transfer and spread of AR genes to pathogens that humans are exposed to through drinking water, irrigation, or recreational activities [4]. Since AR bacteria and AR genes in the environment are poorly understood in comparison to those in humans, animals, and in the clinical setting, it is important to enhance our limited knowledge of AR bacteria in aquatic environments and develop an understanding of the molecular characteristics of the AR determinants [3].
Our recent work demonstrated the prevalence and AR of E. coli from surface water of the Upper Oconee watershed, a mixed-use watershed in northeast Georgia, USA, over a two-year period [5]. The study showed that E. coli are ubiquitous in surface water, and are resistant to antimicrobials commonly used in human and veterinary medicine. In the present study, the genetic basis of AR in these isolates was characterized and the association of the AR determinants with mobile genetic elements were investigated. The goals of this study were to improve understanding of AR E. coli in surface waters and evaluate the potential role of surface waters as a reservoir of, and potential vehicle for, the spread of AR.

PCR Detection of AR Genes and Sequence Analysis
Isolates were tested for the presence of AR genes to which they exhibited phenotypic resistance. Resistant isolates were tested using PCR for genes encoding resistance to: β-lactams, tetracycline, trimethoprim/sulfamethoxazole, sulfisoxazole, chloramphenicol, aminoglycosides, and azithromycin (Table 1) [6][7][8][9][10][11][12]. PCR assays were performed as previously described in the references using whole-cell templates prepared by suspending a single bacterial colony in 200 μL of sterile water. Taq DNA polymerase and PCR nucleotide mix used for PCR assays were purchased from Roche Diagnostics (Indianapolis, IN, USA). PCR conditions for blaCMY were denaturation at 95 °C for 15 min, 30 cycles of denaturation at 94 °C for 1 min, annealing at 61 °C for 1 min, and elongation at 72 °C for 1 min, with a final extension at 72 °C for 10 min. PCR conditions for the amplification of blaCTX-M were similar to blaCMY except the annealing temperature was 54 °C. Negative and positive controls were included in all PCR assays. Amplified PCR products were analyzed using electrophoresis on a 2% agarose gel and visualized by staining with ethidium bromide.
Quinolone and fluoroquinolone resistant isolates were screened for mutations in the quinoloneresistance-determining regions (QRDRs) of gyrA and parC (Table 1) [13,14]. PCR products of the genes were purified using a Qiaquick PCR purification kit (Qiagen, Germantown, MD, USA) according to the manufacturer's directions and used as templates in the sequencing reactions. Sequencing was prepared with 10 μL of water, 8 μL of BigDye Ready Reaction Mix (Applied Biosystems, Foster City, CA, USA), 1 μL of 3.2 pmol forward or reverse primer, and 1 μL of the purified PCR product. Sequencing was performed with the ABI Prism 3130xl Genetic Analyzer (Applied Biosystems)

PCR Detection of AR Genes and Sequence Analysis
Isolates were tested for the presence of AR genes to which they exhibited phenotypic resistance. Resistant isolates were tested using PCR for genes encoding resistance to: β-lactams, tetracycline, trimethoprim/sulfamethoxazole, sulfisoxazole, chloramphenicol, aminoglycosides, and azithromycin (Table 1) [6][7][8][9][10][11][12]. PCR assays were performed as previously described in the references using whole-cell templates prepared by suspending a single bacterial colony in 200 µL of sterile water. Taq DNA polymerase and PCR nucleotide mix used for PCR assays were purchased from Roche Diagnostics (Indianapolis, IN, USA). PCR conditions for bla CMY were denaturation at 95 • C for 15 min, 30 cycles of denaturation at 94 • C for 1 min, annealing at 61 • C for 1 min, and elongation at 72 • C for 1 min, with a final extension at 72 • C for 10 min. PCR conditions for the amplification of bla CTX-M were similar to bla CMY except the annealing temperature was 54 • C. Negative and positive controls were included in all PCR assays. Amplified PCR products were analyzed using electrophoresis on a 2% agarose gel and visualized by staining with ethidium bromide.
Quinolone and fluoroquinolone resistant isolates were screened for mutations in the quinoloneresistance-determining regions (QRDRs) of gyrA and parC (Table 1) [13,14]. PCR products of the genes were purified using a Qiaquick PCR purification kit (Qiagen, Germantown, MD, USA) according to the manufacturer's directions and used as templates in the sequencing reactions. Sequencing was prepared with 10 µL of water, 8 µL of BigDye Ready Reaction Mix (Applied Biosystems, Foster City, CA, USA), 1 µL of 3.2 pmol forward or reverse primer, and 1 µL of the purified PCR product. Sequencing was performed with the ABI Prism 3130xl Genetic Analyzer (Applied Biosystems) following the manufacturer's instructions. Sequence similarity was determined by comparison with the GenBank database using BLAST (www.ncbi.nlm.nih.gov).

Phenotypic and Genotypic Detection of ESBL
Isolates resistant to ceftriaxone (minimum inhibitory concentration (MIC) ≥ 4 mg/L) were considered potential producers of extended-spectrum β-lactamase (ESBL) and selected for further testing. They were assayed phenotypically using cefotaxime/clavulanic acid and ceftazidime/clavulanic acid, and classified as ESBL producers if there was at least a three two-fold decrease of the MIC for ceftazidime or cefotaxime in combination with clavulanic acid compared to the MIC when tested without clavulanic acid [15]. These isolates were genetically characterized via amplification of β-lactamase genes ( Table 1). The PCR products were sequenced using the ABI Prism 3130x Genetic Analyzer and analyzed using BLAST, as described in Section 2.2.

Pulsed-Field Gel Electrophoresis (PFGE)
PFGE was performed as previously described [16]. In brief, plugs were prepared by embedding bacterial genomic DNA in 1.0% Seakem Gold agarose (BioWhittaker Molecular Applications, Rockland, ME, USA) and digested with 10 U of XbaI (Roche Molecular Biochemicals, Indianapolis, USA). Digested DNA was separated via electrophoresis using the CHEF-DRII PFGE system (Bio-Rad, Hercules, CA, USA) in a 0.5x TBE buffer at 6 V for 19 h with ramped pulse times of 2.16 to 54.17 s. Cluster analysis was generated in BioNumerics (Applied Maths, Austin, TX, USA) using the Dice coefficient and the unweighted pair group method of arithmetic averages (UPGMA), with a 1.5% optimization and 1.5% tolerance [17].

Multilocus Sequence Typing (MLST)
MLST was performed using seven housekeeping genes (adk, fumC, gyrB, icd, mdh, purA, and recA), as previously described [18]. PCR products were sequenced using the ABI Prism 3130x Genetic Analyzer (Applied Biosystems), as described in Section 2.2. Sequences were analyzed using BioNumerics (Applied Maths) and sequence types (STs) were assigned through the Center for Genomic Epidemiology [19]. The class 1 integron was detected via amplification of the conserved segment of the integrase gene, intI, as previously described (Table 1) [20]. PCR conditions consisted of 30 cycles of denaturation at 94 • C for 1 min, annealing at 63 • C for 1 min, elongation at 72 • C for 2 min, and a final extension at 72 • C for 10 min. PCR products were analyzed using electrophoresis, as described in Section 2.2.
Analysis of the QRDRs of gyrA and parC was performed on the five E. coli isolates resistant to nalidixic acid. All five isolates contained a mutation of serine-83 to leucine in gyrA; one isolate also had aspartic acid-87 mutated to asparagine (Table 3). Additional gyrA mutations were seen outside the QRDR, including a lysine-162 to glutamine mutation and a valine-37 to leucine mutation. Of the five nalidixic-acid-resistant isolates, one was also resistant to ciprofloxacin and had a mutation of serine-80 to isoleucine in the QRDR of parC. Three isolates had single mutations in parC outside the QRDR, two isolates with a mutation of lysine-247 to glutamic acid and one with a mutation of alanine-192 to glycine ( Table 3). The remaining nalidixic-acid-resistant isolate did not carry any parC mutation.

ESBL Detection
The results of the phenotypic assay confirmed the presence of one ESBL-producing E. coli. Upon the amplification and sequencing of β-lactamase genes, the ESBL-producing E. coli was positive for bla CTX-M-15 and bla TEM-1 , while the non-ESBL producer was positive for bla CMY-2 and bla TEM-1 (Table 2  and Supplementary Materials Table S1).

Molecular Characteristics
PFGE revealed only two isolates with indistinguishable PFGE patterns; however, they differed in other characteristics, including AR patterns and the plasmid replicons detected (Figure 2). E. coli isolates were previously assigned phylogenetic groups [5], and the result is included in the dendrogram for comparison with PFGE patterns and other data collected in the current study ( Figure 2).

Mobile Genetic Elements
Most of the E. coli isolates (28/34; 82.4%) were positive for one or more plasmid replicons ( Figure  2, Supplementary Materials Table S1). Out of the 28 replicons tested using PCR, 11 types (A/C, FIA, FIB, FIC, FII, HI1, I1α, P, R, X1, Y) were identified, with FIB being the most common, carried by about half of the resistant E. coli isolates (n = 16). FII was the second-most common replicon (n = 11), followed by FIA (n = 4), HI1 (n = 4), and I1α (n = 3). P, A/C, and Y were present in two isolates each, while X1, R, and FIC were represented only once. Class I integron (intI1) was detected in three isolates, all of which carried plasmid replicons as well.

Discussion
The Upper Oconee watershed in Northeast Georgia, USA, is a mixed-use watershed including relatively pristine headwater streams, as well as streams influenced by agricultural runoff and contaminated effluents from wastewater treatment plants, failing septic systems, and sewer line leaks. This mixture of relatively pristine and highly developed land use makes this watershed a useful proxy for other similar-sized watersheds in the southeastern USA. This study determined the molecular characteristics of AR determinants and mobile genetic elements (MGEs) in this watershed

Mobile Genetic Elements
Most of the E. coli isolates (28/34; 82.4%) were positive for one or more plasmid replicons (Figure 2, Supplementary Materials Table S1). Out of the 28 replicons tested using PCR, 11 types (A/C, FIA, FIB, FIC, FII, HI1, I1α, P, R, X1, Y) were identified, with FIB being the most common, carried by about half of the resistant E. coli isolates (n = 16). FII was the second-most common replicon (n = 11), followed by FIA (n = 4), HI1 (n = 4), and I1α (n = 3). P, A/C, and Y were present in two isolates each, while X1, R, and FIC were represented only once. Class I integron (intI1) was detected in three isolates, all of which carried plasmid replicons as well.

Discussion
The Upper Oconee watershed in Northeast Georgia, USA, is a mixed-use watershed including relatively pristine headwater streams, as well as streams influenced by agricultural runoff and contaminated effluents from wastewater treatment plants, failing septic systems, and sewer line leaks. This mixture of relatively pristine and highly developed land use makes this watershed a useful proxy for other similar-sized watersheds in the southeastern USA. This study determined the molecular characteristics of AR determinants and mobile genetic elements (MGEs) in this watershed to improve our understanding of the watershed as a catchment for AR, an exchange point of AR genes, and a potential source of exposure for humans and animals to AR bacteria.
This study revealed 17 genes in the 34 E. coli isolates responsible for their phenotypic resistance to the antimicrobials tested. Tetracycline resistance was predominant in the isolates, with tetA most frequently detected. When compared to studies conducted in different parts of the world, our findings show similar results with tetA being detected most often in E. coli from aquatic environments; however, tetM was not detected here but was frequently detected in those studies [21][22][23]. Ampicillin and sulfisoxazole resistance could be mostly attributed to bla TEM and sul2, respectively. Similar prevalence of AR genes was seen in E. coli isolates from other aquatic environments [21][22][23]. However, unlike those previous findings in which cat1, aadA, and dhfr1 and dhfr7 were responsible for chloramphenicol, streptomycin, and trimethoprim resistance, respectively, our findings suggested floR, strA and strB, and dhfr5 were responsible for resistance to those antimicrobials [21][22][23]. A plasmid-borne azithromycin resistance gene, mph(A), was detected in two azithromycin-resistant isolates. A study conducted by Nguyen et al. reported that mph(A) was the most common macrolide resistance gene among commensal and clinical isolates of E. coli from five countries on four continents [12].
Quinolone and fluoroquinolone resistances are commonly mediated by mutations in the QRDR of gyrA and parC, which are defined as codons 67-106 of gyrA and codons 56-108 of parC [24]. All five nalidixic-acid-resistant E. coli isolates carried a Ser-83→Leu substitution in gyrA; the isolate which was also resistant to ciprofloxacin carried Asp-87→Asn substitution in gyrA as well as Ser-80→Ile substitution in parC. This is consistent with the view that a single mutation in gyrA can generate nalidixic acid resistance, but additional mutations in gyrA and/or parC are needed for high-level resistance to ciprofloxacin [24]. In addition to the mutations within the QRDR of gyrA and parC, mutations were identified outside of the QRDR. However, it is uncertain whether these mutations would contribute to resistance to quinolones and fluoroquinolones.
The most notable result from this study is the presence of E. coli belonging to ST131 in the surface water. ST131 is a globally disseminated clone that causes a wide range of infections, including urinary tract and bloodstream infections, in community and hospital settings [25]. Its multidrug resistance (MDR: resistant to two or more antimicrobial drugs), enhanced virulence, and rapid dissemination have made this strain of E. coli a significant public health threat worldwide [25]. The three ST131 isolates in this study were recovered from different seasons and in different locations; however, they shared many common characteristics. The three isolates were resistant to ampicillin and nalidixic acid, belonged to phylogenetic group B2, contained bla TEM , had mutations in gyrA and parC, and carried an IncF plasmid that was positive for the replicon FIB alone or along with the FII replicon. The shared resistance to ampicillin was likely mediated by bla TEM , which encodes TEM β-lactamase, usually located on an IncF plasmid [25]. In addition, reduced susceptibility to ciprofloxacin was seen in these three isolates, with the MICs ranging from 0.25 mg/L to >4 mg/L compared to other isolates from this study, whose MICs ranged from ≤0.015 mg/L to 0.03 mg/L. Only one of the three isolates was resistant to ciprofloxacin according to the Clinical Laboratory Standards Institute (CLSI) guideline (≥4.0 mg/L) [15]; however, more than a tenfold increase in the MICs of the other two isolates is significant as ciprofloxacin resistance has been commonly detected in ST131, limiting treatment options for infections caused by ST131 E. coli [25]. Moreover, fluoroquinolone-susceptible E. coli isolates of ST131 were identified in urinary tract infection patients, as well as in healthy populations [25]. In addition to the mutation in gyrA (Ser-83→Leu), the two ciprofloxacin-susceptible isolates also contained the Lys-247→Glu substitution in parC. This mutation outside the QRDR of parC could be responsible for the reduced susceptibility to ciprofloxacin in addition to the resistance to nalidixic acid in these isolates. All three ST131 isolates belonged to different pulsotypes, confirming the clonal diversity within ST131.
Of the three ST131 E. coli isolates, only one isolate encoded CTX-M-15. Among the diverse subclones of ST131, CTX-M-15-producing E. coli is the most widely distributed strain worldwide [26]. Since its first detection in India in 2001, this pandemic clone has been responsible for community and hospital-acquired infections [26]. Unlike the other two non-ESBL-producing ST131 isolates, the CTX-M-15 ESBL-producing ST131 was resistant to third-generation cephalosporins and had a reduced susceptibility to amoxicillin/clavulanic acid.
In addition to the ST131 E. coli isolates, an isolate positive for bla CMY-2 was identified. CMY-2 is the most commonly identified plasmid-mediated ampicillin (AmpC) β-lactamase across the world [27]. The bla CMY-2 -positive isolate was resistant to a broad spectrum of β-lactams, but not inhibited by clavulanic acid, contained bla TEM-1 , and exhibited resistance to multiple drugs (amoxicillin/clavulanic acid, ampicillin, cefoxitin, ceftiofur, ceftriaxone, and gentamicin). I1α and FIB replicon types were detected in the isolate, similar to the previous findings that bla CMY-2 is often present on Inc1 and IncF plasmids [28,29]. The isolate belonged to virulence-associated phylogenetic group B2 and corresponded to ST2552. The bla CMY-2 gene has often been detected in E. coli from food animals and their products throughout the world, which could be attributed to the agricultural use of expanded-spectrum cephalosporins in food animals [29,30].
Among the diverse STs seen in this study, the presence of ST10, ST58, ST69, ST86, ST88, and ST117 strains is notable. Even though these isolates were not ESBL producers, E. coli that belonged to these STs were present in other water sources, as well as human and animal clinical isolates as ESBL-producing E. coli in Netherlands and France [31,32]. Furthermore, the two ST69 isolates exhibited ampicillin resistance and contained bla TEM . ST10, ST58, and ST69 were each represented twice in this study, but the isolates of the same STs displayed different phenotypic and genotypic profiles. The three sets of matching isolates each belonged to the same phylogenetic group (ST10 to C, ST58 to B1, and ST69 to E), and contained IncF plasmids, but had different AR phenotypic profiles, AR genes, PFGE, and replicon type (RT) profiles. This demonstrates the diversity of E. coli in surface water.
MGEs, such as plasmids and integrons, are readily acquired by E. coli often conferring resistance in these bacteria [33]. These MGEs can be transferred between organisms of the same species or different genera, mediating the exchanges of AR genes in the environment. Our results showed that MGEs capable of such exchanges are present among 28 of the 34 AR waterborne E. coli. IncF plasmids were found in 20 isolates, nine of which carried more than one F replicon. FIB was the most common replicon, and was often detected in combination with FIA and/or FII replicons. Of nine E. coli isolates containing the TEM β-lactamase, eight isolates contained IncF plasmids, suggesting the possible carriage of bla TEM on an IncF plasmid. Other plasmid types detected in this study were IncA/C, IncHI1, IncI1α, IncP, IncR, IncX1, and IncY. Among these plasmids, IncA/C, IncF, and IncI1 are reported to be highly associated with multiple resistance [34].
Integrons are also known to be associated with AR gene acquisition and dissemination; class 1 integrons are the most commonly identified with multiple resistance genes [33,35]. Integrons are not mobile by themselves but can be mobilized by other MGEs, such as transposons and plasmids, and can spread to other bacterial species [35]. Of the 15 MDR E. coli isolates from this study, three isolates carried class 1 integrons (20%; 3/15). This prevalence is comparable to studies conducted in the Rio Grande River in the Texas-Mexico region and Seine estuary in France, which identified class 1 integrons in 12.5% (4/32) and 8.9% (25/279) of the MDR E. coli isolated, respectively [36,37].
In this study, 34 AR E. coli isolates, none of which were clones, were recovered from 24 sampling sites from the Upper Oconee watershed near Athens, GA. Land uses draining to the sampling sites include areas of urban, suburban, exurban, and rural development, as well as industrial, agricultural, and medical facilities. The AR isolates and the AR genes seem to be randomly distributed around the watershed rather than being clustered in specific regions or only found in areas where there might be more usage of antimicrobial drugs. Several studies proposed municipal and hospital wastewaters as the main source of AR bacteria, including ESBL-producing E. coli, in aquatic environments [31,38]. Other studies suggested animal manure and feces from farm animals and wildlife may also be contributors, though to a lesser extent [22,31,39]. In this study, a CTX-M-15 ESBL-producing ST131 isolate was recovered from a sampling site downstream of a hospital (MIDO 826), a potential source of the pathogenic bacteria ( Figure 3). Interestingly, ESBL-producing E. coli were not isolated at the sampling site immediately downstream of the hospital (MIDO 825). This suggests a more complex method of AR transference to E. coli. Studies conducted in Nebraska and South Carolina, USA, found that AR bacteria were also recovered in environments with low or no fecal or antimicrobial inputs [39,40]. This suggests the persistence and wide distribution of AR genes in the aquatic environment regardless of the degree of antibiotic selective pressure.  [39,40]. This suggests the persistence and wide distribution of AR genes in the aquatic environment regardless of the degree of antibiotic selective pressure. It is important to note that our methods did not use selection with antimicrobials to isolate E. coli, thus the 6.9% resistant isolates is most likely a true representation of the levels of AR E. coli in the streams near Athens, GA, which is not trivial. In separate on-going studies when selective pressure is applied with various antimicrobials during isolation, almost all water samples yielded resistant E. coli isolates (data not shown). The presence of AR bacteria in surface waters is a significant public health concern as surface water serves as a source of drinking water, is used for recreational activities, and is also used for irrigation of agricultural crops and water for food animals. Humans can be exposed to AR bacteria through contact with contaminated water sources. Likewise, livestock and wildlife animals can also be exposed through contact with contaminated water sources, further spreading these bacteria. Thus, aquatic environments serve as the interface, which brings humans, animals, and environments together, facilitating the spread of AR in between these compartments.

Conclusions
The present study identified diverse strains of AR E. coli in surface waters, including an epidemic strain. A CTX-M-15 ESBL-producing ST131 E. coli was isolated, and to our best knowledge, this is the first report of the presence of this particular strain in surface water in the USA. AR E. coli can transfer their AR determinants to other bacteria, which can then be transferred to humans. The presence of MGEs, such as plasmids and integrons, in AR E. coli would increase the chances of AR gene dissemination in the environment. The identification of surface water as a reservoir of AR for human and veterinary antimicrobial drugs highlights the importance of continuous surveillance of AR bacteria in surface water. It is important to note that our methods did not use selection with antimicrobials to isolate E. coli, thus the 6.9% resistant isolates is most likely a true representation of the levels of AR E. coli in the streams near Athens, GA, which is not trivial. In separate on-going studies when selective pressure is applied with various antimicrobials during isolation, almost all water samples yielded resistant E. coli isolates (data not shown). The presence of AR bacteria in surface waters is a significant public health concern as surface water serves as a source of drinking water, is used for recreational activities, and is also used for irrigation of agricultural crops and water for food animals. Humans can be exposed to AR bacteria through contact with contaminated water sources. Likewise, livestock and wildlife animals can also be exposed through contact with contaminated water sources, further spreading these bacteria. Thus, aquatic environments serve as the interface, which brings humans, animals, and environments together, facilitating the spread of AR in between these compartments.

Conclusions
The present study identified diverse strains of AR E. coli in surface waters, including an epidemic strain. A CTX-M-15 ESBL-producing ST131 E. coli was isolated, and to our best knowledge, this is the first report of the presence of this particular strain in surface water in the USA. AR E. coli can transfer their AR determinants to other bacteria, which can then be transferred to humans. The presence of MGEs, such as plasmids and integrons, in AR E. coli would increase the chances of AR gene dissemination in the environment. The identification of surface water as a reservoir of AR for human and veterinary antimicrobial drugs highlights the importance of continuous surveillance of AR bacteria in surface water.