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Article

Distribution and Genotyping of Aquatic Acinetobacter baumannii Strains Isolated from the Puzi River and Its Tributaries Near Areas of Livestock Farming

by
Hsin-Chi Tsai
1,2,
Ming-Yuan Chou
3,†,
Yi-Jia Shih
4,5,6,†,
Tung-Yi Huang
4,†,
Pei-Yu Yang
7,†,
Yi-Chou Chiu
8,
Jung-Sheng Chen
4 and
Bing-Mu Hsu
4,9,*
1
Department of Psychiatry, School of Medicine, Tzu Chi University, Hualien 970, Taiwan
2
Department of Psychiatry, Buddhist Tzu-Chi General Hospital, Hualien 970, Taiwan
3
Department of Internal Medicine, Cheng Hsin Hospital, Taipei 111, Taiwan
4
Department of Earth and Environmental Sciences, National Chung Cheng University, Chiayi 621, Taiwan
5
Department of Biotechnology, Xiamen Ocean Vocational College, Xiamen 361000, China
6
Fisheries College, Jimei University, Xiamen 361000, China
7
Department of Laboratory, Show Chwan Memorial Hospital, Changhua 500, Taiwan
8
General Surgery, Surgical Department, Cheng Hsin General Hospital, Taipei 111, Taiwan
9
Center for Innovative on Aging Society (CIRAS), National Chung Cheng University, Chiayi 621, Taiwan
*
Author to whom correspondence should be addressed.
†
Ming-Yuan Chou, Yi-Jia Shih, Tung-Yi Huang and Pei-Yu Yang have equal contributions to the first author.
Water 2018, 10(10), 1374; https://doi.org/10.3390/w10101374
Submission received: 1 July 2018 / Revised: 10 August 2018 / Accepted: 28 September 2018 / Published: 1 October 2018
(This article belongs to the Special Issue Antimicrobial Resistance in Environmental Waters)
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Abstract

Acinetobacter baumannii is an important health care-associated bacterium and a common multidrug-resistant pathogen. The use of antibiotics in the husbandry industry has raised concerns about drug-resistant A. baumannii strains, which may affect humans. This study aimed to investigate the seasonal distribution of A. baumannii in aquatic environments near areas of livestock farming. The geographic distribution, antibiotic resistance characteristic, and DNA fingerprinting genotype of A. baumannii were also studied. The results showed that environmental A. baumannii was prevalent during the summer and autumn. The hotspots for A. baumannii were found at the sampling sites of livestock wastewater channels (21.4%; 3/14) and the tributaries adjacent to livestock farms (15.4%; 2/13). The prevalence of A. baumannii at these locations was significantly higher than those adjacent to the Puzi River. Multidrug-resistant strain of A. baumannii was not found in this study, with only one strain (5%; 1/20) being resistant to tetracycline. Of the isolates that were obtained, 10% (2/20) and 20% (4/20) were found to be intermediately resistant to tetracycline and sulphamethoxazole/trimethoprim, respectively. The genotyping patterns and clustering analysis indicated that enterobacterial repetitive intergenic consensus sequence polymerase chain reaction (ERIC-PCR) differentiated A. baumannii strains effectively. There were two major clusters that could then be subtyped into 20 A. baumannii strains with 15 profiles. The A. baumannii strains that were isolated from upstream of the Puzi River and livestock wastewater channels were composed of Cluster I. Cluster II only contained isolates from downstream of the Puzi River area. Furthermore, isolates from adjacent sites were shown to have identical profiles (100%). These results suggest that A. baumannii may have spread through free-flowing water in this study. Therefore, we propose that livestock wastewater is one of the sources that contribute to A. baumannii pollution in water bodies. In summary, continuous monitoring of antibiotic pollution in livestock wastewater is required.

1. Introduction

Acinetobacter baumannii is a Gram-negative, non-fermenting, aerobic bacterium [1,2,3] which is considered to be ubiquitous as it can be recovered from various environments, including soil or surface water [4,5,6,7]. It is also an important health care-associated pathogen, which mostly causes opportunistic infections in immunocompromised individuals [6]. The most prevalent symptoms that are caused by A. baumannii in hospitals include urinary tract infection, meningitis, bacteraemia, peritonitis, surgical wound infection, and pneumonia [4,8,9]. Many studies have surveyed the mortality rate of the pathogen, which ranged from 5% in general wards to more than 60% in patients suffering from multidrug-resistant A. baumannii infections [8,10]. In the treatment of various A. baumannii infections, a reliable method for identification and characterization of the strains is necessary. Numerous methods have been developed for analysis and molecular typing of A. baumannii, such as plasmid analysis, ribotyping, multilocus sequence genotyping (MLST), pulsed-field gel electrophoresis (PFGE), and several other sequence-based polymerase chain reaction (PCR) typing techniques [2,4,6,11,12,13]. Despite MLST and PFGE being highly discriminative genotyping methods, sequence-based DNA fingerprinting PCR techniques have advantages of performance ease and economic viability [2,12,14]. Since the enterobacterial repetitive intergenic consensus polymerase chain reaction (ERIC-PCR) technique has a sound discrimination index (over 94%) [12] and a relatively low cost for large-scale genotyping of A. baumannii when compared with other sequence-based PCR techniques, it has been widely adopted in the studies of environmental A. baumannii studies.
Multidrug-resistant A. baumannii (MDR-AB) is referred to as resistance to three out of four antibiotic classes, namely ceftazidime, ciprofloxacin, gentamicin, and imipenem [15]. As the scale of antibiotic adoption in clinical treatment increases, the presence of MDR-AB also increases, which poses a great challenge for public health; therefore, surveillance of environmental A. baumannii is urgent [8,16]. Recently, it has been reported that the incidence of nosocomial MDR-AB infection has elevated significantly. As such, the presence of MDR-AB in the environment could increase the risk of infection [8,17,18,19].
A. baumannii exists not only in hospitals, but also in its natural habitats, such as soil, surface water, human skin, and inorganic surfaces [6,20,21,22,23]. Antimicrobial agents are widely used in livestock and aquaculture to suppress the growth of bacteria and to boost survival rates [24,25,26]. However, residue antibiotic agents from various sources, such as waste animal feed and animal excrement, can leak into the environment as active ingredients. Indeed, environmental studies have proven that there were substantial amounts of various antibiotic compounds in soils [27]. Long-term antibiotic contamination can change the gene profile of bacteria in livestock and natural habitats. For example, sulfonamide-resistance genes (sul1, sul2, and sul3) have commonly been found in aquatic environments in northern Vietnam, and they have been isolated from the excrement of pigs suffering from diarrhea in Ontario [28,29]. These reports provide evidence that the use of antibiotics in the husbandry industry may promote the emergence of antibiotic-resistant bacteria. The most commonly used livestock-associated antibiotic classes include aminoglycosides, cephalosporins, chloramphenicol, lincosamides, macrolides, penicillins, polyether ionophores, polypeptides, and tetracyclines, with tetracyclines and macrolides combined products as the most frequently used antibiotic agents [24,30,31,32]. The increased use of antibiotics in livestock and aquaculture could lead to an increase in the population of antibiotic-resistant A. baumannii strains, causing the environment to act as a reservoir of these populations [26].
In recent years, many studies have focused on the epidemiology and analysis of antibiotic resistance, resistance mechanisms, and novel treatments of A. baumannii [4,6,19,33]. However, evaluations on the impact of antibiotic usage on the environment were less clear. Many studies have revealed that antibiotic residues can be observed in liquid manure from pig husbandries, suggesting that microorganisms surrounding the aquatic environment near these husbandries are affected by these antibiotic residues and result in the risk of natural selection of these antibiotic-resistant pathogens from the environment. The aim of this study was to understand the seasonal variability and antibiotic susceptibility profiles of A. baumannii in the Puzi River and its tributaries near areas of livestock farming and to characterise A. baumannii in aquatic environments using the ERIC-PCR method.

2. Materials and Methods

2.1. Collection and Concentration of Water Samples

Monthly water samples were collected from the Puzi River from May 2014 to April 2015. Water samples were collected from 32 locations. Subsequently, these 32 locations were separated into three areas based on our previous studies [34] (Figure 1); sites PR01–PR12 (Area A) are located upstream of the Puzi River, sites PR14–PR25 (Area B) are located midstream, and sites PR26–PR34 (Area C) are located downstream. Additionally, water samples from the livestock wastewater channel, household wastewater channel, and tributary were collected at 30 locations around the Puzi River in October 2015. The sampling sites are summarised in Figure 2. At each sampling site, a water sample of approximately 3000 mL was collected for pathogen detection. Each water sample was stored in three sterile one-litre bottles and was transported to the laboratory at 4 °C within 24 h for analysis.
For the detection of specific microbial pathogens, 300 mL of each water sample was filtered through 47 mm GN-6 membranes (Pall, Mexico City, Mexico) with a pore size of 0.45 μm, in a stainless steel filter holder. Subsequently, the membranes were used for sample enrichment of each specific pathogen.

2.2. Enrichment and Identification of A. baumannii

For A. baumannii enrichment, the samples that remained on the membranes after filtration were cultured in MacConkey Broth (HIMEDIA, M007, Taipei, Taiwan). Each sample was selectively cultured on CHROMagar™ Acinetobacter (CHROMagar, Paris, France) and 5% sheep blood agar (TPM, TPM150M, Taiwan). Subsequently, the agar plates were incubated at 30 °C for 24 h.
DNA extraction was performed using 1 mL of the concentrated pellet from MacConkey Broth (including each suspected isolate from CHROMagar™ Acinetobacter agar that underwent re-amplification), using a MagPurix 12s Automated Nucleic Acid Purification System (Zinexts Life Science Corp., New Taipei City, Taiwan) for automated DNA extraction and a MagPurix Viral DNA Extraction Kit ZP02006, according to the manufacturer’s manual. Total DNA eluate of A. baumannii (2 μL) was mixed with primers (1 μL, 0.4 μM), 5 μL of Fast-Run Taq Master Mix with Dye, and 16 μL of deionised water to yield a final reaction volume of 25 μL. The primers that were used in this study were P-Ab-ITSF: 5′-CAT TAT CAC GGT AAT TAG TG-3′ and P-AbI-TSB: 5′-AGA GCA CTG TGC ACT TAA G-3′ [35]. The amplification reaction was performed as follows: denaturation for 5 min at 94 °C, followed by 30 cycles of 30 s at 95 °C, 30 s at 52 °C, and 30 s at 72 °C, and a final extension step at 72 °C for 7 min. For A. baumannii detection, positive control DNA (A. baumannii, ATCC 19606) was also included in each run. The PCR products were electrophoresed on a 2% agarose gel (Biobasic Inc., Markham, ON, Canada), were stained with an ethidium bromide solution, and were visualised under UV light.

2.3. ERIC-PCR for A. baumannii

ERIC-PCR was performed as described by Soni et al. with modifications [36]. The primers ERIC-1 (5′-ATG TAA GCT CCT GGG GAT TCA C-3′) and ERIC-2 (5′-AAG TAA GTG ACT GGG GTG AGC G-3′) were synthesised to amplify the ERIC-PCR fingerprints of A. baumannii. The PCR mixture (25 μL) was comprising of 200 μM of each deoxy-ribonucleotide triphosphate (dNTP), 1.8 U of Taq polymerase (Biolabs, Ipswich, MA, USA), 3 mM of MgCl2, 10 mM of Tris-HCl (pH = 9.0), 1.0 μM of each primer, and 50 ng of the DNA templates. An additional amount of sterile distilled water was added to attain a volume of 50 μL. The amplification reaction was performed as follows: denaturation for 7 min at 95 °C, followed by 30 cycles of 1 min at 95 °C, 1 min at 52 °C, and 8 min at 65 °C, and a final extension step at 65 °C for 10 min. The ERIC-PCR products were electrophoresed on a 1.5% agarose gel (Biobasic Inc., Markham, Canada) containing Tris-acetate-EDTA (TAE) and 1 μg/mL ethidium bromide at 100 V for 30 min. Subsequently, they were visualised with a UV transilluminator to obtain photographs.
Additionally, the ERIC-PCR patterns were analysed with the Bionumerics software package (Applied Maths, Austin, TX, USA). The relationship between two given isolates was scored using the Jaccard similarity coefficient, and isolates were clustered based on their inter-isolation similarities using the unweighted pair group method with arithmetic averages.

2.4. Antibiotic Susceptibility of A. baumannii

All A. baumannii isolates were tested for antibiotic susceptibility by performing the Kirby–Bauer disk diffusion test on Mueller–Hinton agar plates (Becton, Dickinson and Company, Franklin Lakes, NJ, USA) according to the Clinical & Laboratory Standards Institute (CLSI) [37]. The antibiotics and their dosages that were used for testing in this study included: ciprofloxacin (5 μg), cefepime (30 μg), gentamicin (10 μg), imipenem (10 μg), ampicillin/sulbactam (20/10 μg), sulphamethoxazole/trimethoprim (SXT) (23.75/1.75 μg), and tetracycline (30 μg).

3. Results and Discussion

3.1. Presence of A. baumannii in the Aquatic Environment

The observed presence of A. baumannii is summarised in Table 1. The results showed that its detection rate was 3.8% annually, and that it was most prevalent in May, July, August, and September 2015. The detection rate was highest in May (20.8%), followed by July (12.5%). The results indicated that this pathogen occurred more frequently during the summer in aquatic environments. This observation is in accordance with the results of previous studies, which have suggested that A. baumannii is strictly aerobic and thermotropic (37–42 °C) [6,21,38]. Furthermore, another study suggested that, during the past decade, the prevalence of this pathogen in hospitals was higher between July and October than between January and June [39]. Moreover, Chu et al. found that in Hong Kong, 53% of medical students and new nurses were colonised with Acinetobacter during the summer, compared to 32% in winter [40]. The present study is the first to report the annual distribution of A. baumannii and its seasonal fluctuations in natural environments.
The Puzi River was separated into three areas (Figure 1). The highest detection rate of A. baumannii was found in Area A (5.2%), followed by Area B (4.2%), while the detection rate in Area C was significantly lower (Table 2). The upstream region of the Puzi River (Area A) displayed the highest annual prevalence. Therefore, wastewaters from different sources, including livestock wastewater channels and tributaries of the Puzi River near livestock farming areas, were sampled to investigate the prevalence of A. baumannii in October 2014. The results are shown in Table 2. The detection rate of the pathogen was 21.4% (3/14) in livestock wastewater channels and 15.4% (2/13) in the tributaries of the Puzi River. However, the pathogen was not detected in household wastewater. Figure 2 shows the location of livestock farmlands near the Puzi River. The main location of livestock farming was distributed upstream of the Puzi River (57%; 8/14), and the wastewater outlet also flowed into the Puzi River tributaries. These results suggested that A. baumannii was transmitted from livestock wastewater into the natural aquatic environment, since the detection rate of this pathogen was higher in wastewater than in the main river. The highest prevalence of A. baumannii was in the area upstream of the Puzi River basin. Furthermore, 36% (5/14) of livestock farmland was distributed in the area downstream of the Puzi River basin, which is close to the estuarine environment, where conditions might not be optimal for A. baumannii growth.
Fernando et al. investigated and isolated A. baumannii from a river and nearby dairy farms [38]. Additionally, there are reports that A. baumannii isolates, which carried the BLAOXA-23 carbapenemase gene, were isolated from the Seine River in downtown Paris [41] and from the Tietê and Pinheiros rivers in Brazil [42]. Nevertheless, the seasonal distribution and sources of this pathogen remain largely unknown. In previous studies, this organism has primarily been investigated in hospitals and the clinical environment. The results of these studies have consistently indicated that A. baumannii is widespread in nosocomial environments [4,17,43]. This organism also prefers to grow in humid conditions. Therefore, the clinical environment acts as a reservoir of A. baumannii and leads to opportunistic infections in humans [9,44,45]. However, different places in the natural environment, such as rivers, soil, storage tanks in dairy farms, and manure, can also serve as reservoirs for this pathogen [38]. This study first summarises the observed seasonal prevalence of A. baumannii in the aquatic environment. The results show that the hotspot basin environment for this pathogen is livestock wastewater. We suggest that the wastewater from livestock farming is a reservoir for A. baumannii. Further, this pathogen spreads into the Puzi River tributary and agricultural irrigation canals through the wastewater that is discharged from livestock wastewater channels. However, the prevalence of A. baumannii that was observed in this environmental survey remained lower than that observed in hospital studies. One possible explanation for this result is that the aquatic environment is constantly changing and, consequently, flowing water does not act as a good reservoir for this microorganism.

3.2. Antimicrobial Susceptibility

A total of 20 A. baumannii-positive samples were isolated from 318 water samples, which were dispersed in 16 locations out of 32 research sites (Figure 1 and Figure 2). The results of the antibiotic susceptibility tests in A. baumannii-positive samples are summarised in Table 3. The results show that the positive control strain (ATCC-16906) was highly resistant to SXT, intermediately resistant to tetracycline, and sensitive to other antibiotic agents (Table 4). In addition, the A. baumannii-GI-G11511 strain that was isolated from livestock wastewater was resistant to tetracycline. The A. baumannii-GI-IM0611 strain, which was isolated from the Puzi River tributary and agricultural irrigation canals, was also found to be intermediately resistant to tetracycline. Four strains (A. baumannii PR07-0531, 09-0531, 22-0511, and 23-0521) were isolated from the Puzi River, and they were found to be intermediately resistant to SXT. Additionally, one strain, A. baumannii-PR22-0511, was also found to be intermediately resistant to tetracycline. The other 14 environmental strains were found to be susceptible to all antibiotic agents. These results indicate that most of the isolated strains are quite susceptible to tetracycline. Only 5% (1/20) of the analysed strains were resistant to, and 10% (2/20) intermediately resistant to, tetracycline. Only four strains (20%; 4/20) showed intermediate resistance to SXT. Additionally, no multidrug-resistant A. baumannii (MDR-AB) was observed in the aquatic environment. The results for antibiotic susceptibility imply that the A. baumannii that is present in the aquatic environment differs from the A. baumannii in hospitals, based on the multidrug-resistant outcome. Therefore, we will analyse the homology between the MDR-AB strains from local hospitals and aquatic environments in our future studies.
To conclude the results, it can be said that the environmental A. baumannii strains in this study showed much lower antibiotic resistance than hospital A. baumannii. The results also indicated that the strains that were present in water samples were quite susceptible to, and/or intermediately resistant to, certain antibiotics, including SXT and tetracycline. Previous studies have demonstrated that tetracyclines and SXT are the common classes of antimicrobials that are used in livestock [24,26]. Our observations indicate potential mechanisms by which the frequent use of agricultural antibiotics may lead to the formation of antibiotic-resistant bacteria strains. Such strains also pose potential risks to humans, through the direct transmission of the resistant bacteria by water sources or the transfer of resistance genes from antibiotic-resistant bacteria in the agricultural environment into human pathogens [42,46]. Therefore, it is necessary to understand the mechanism of transmission of MDR-AB strains into aquatic environments. In future studies, we will not only focus on understanding the association between agricultural antibiotic usage conditions and the environmental prevalence of MDR-AB, but also on the analysis of homology between MDR-AB strains from local hospitals and aquatic environments.

3.3. ERIC-PCR Fingerprint Analysis

A total of 20 A. baumannii strains were further characterised for strain genotyping and were compared with a reference strain (ATCC 16906) using ERIC-PCR analysis. Five isolates were collected from livestock wastewater and the Puzi River tributaries near livestock farming areas, and 15 isolates were collected from the Puzi River basin. The standard that was used to determine the degree of similarity between different ERIC-PCR fingerprints was based on similarities between the reference strains and the samples from the different A. baumannii colonies at the same sampling sites (Site No. PR05, 07, 12, and 25). According to the ERIC-PCR analysis, the Jaccard similarity coefficient between the two reference strains was 85%. The isolates from different colonisation areas at the four sampling sites (A. baumannii-PR12-0911 vs. A. baumannii-PR12-0912, A. baumannii-PR05-0911 vs. A. baumannii-PR05-0912, A. baumannii-PR25-0811 vs. A. baumannii-PR25-0821, and A. baumannii-PR07-0711 vs. A. baumannii-PR07-0721) showed a Jaccard similarity coefficient of 100%, which was used to confirm the genotyping (Figure 3). Two major clusters were observed at a similarity level of less than 20%, and 20 A. baumannii strains were subtyped into 15 profiles. The results also showed that the strains from Area A of the Puzi River were similar to the livestock wastewater and belonged to cluster I (bootstrap value (p-value) = 90%). Further, cluster II contained isolates from the other Puzi River area (p-value = 90%) (Figure 3). Maleki et al. (2016) found that the diversity of genetic patterns of A. baumannii that were observed by ERIC-PCR analysis was due to the wide distribution in hospitals [2]. Here, we postulate that this high diversity is due to the distributions of sampling sites with different sources. Strains A. baumannii-PR22-0511 and A. baumannii-PR23-0521 from two adjacent sampling sites showed an identical profile (100% similarity). This result suggests that one mechanism of A. baumannii transmission is through free-flowing water, which leads to spreading to other aquatic environments.
We regard the genotyping of A. baumannii isolates as a necessary means to control the epidemic that has been caused by this organism. Therefore, different DNA fingerprinting techniques have been developed for the quick and accurate classification of A. baumannii isolates. Molecular genotyping methods, including plasmid profiling, ribotyping, PFGE, MLST, and PCR-based typing methods, have been evaluated as potential methods to characterise A. baumannii isolates [6]. Despite MLST and PFGE being highly discriminative genotyping methods, PCR-based DNA fingerprinting techniques have advantages of performance ease and economic viability [2,6,12]. To date, there have been many studies describing different PCR-based methods to type MDR-AB [47,48,49]. In general, the ERIC-PCR method is a common, easy, and quick fingerprinting technique for characterising A. baumannii isolates [2,48,49]. The results of this study indicate that the ERIC-PCR method is useful for the analysis of genetic variation among environmental A. baumannii isolates.

4. Conclusions

In this study, we first investigated the seasonal temporal distribution and antibiotic resistance of A. baumannii in natural aquatic environments. In conclusion, the seasonal prevalence of A. baumannii and the percentage of antibiotic-resistant A. baumannii isolates in water bodies were found to be lower than those in known nosocomial environments. However, we observed that the highest detection rate of A. baumannii occurred in livestock wastewater. We also observed one tetracycline-resistant strain. In addition, four strains were found to be intermediately resistant to SXT, and one was intermediately resistant to tetracycline. These results indicate the necessity of monitoring on the use of antimicrobials in livestock. Further, livestock wastewater is a potential source of A. baumannii contamination. This is an important issue for the transmission pathway of A. baumannii between the environment and hospitals, or even long-term care facilities, and is worth further exploration.

Author Contributions

Conceptualization, B.-M.H and H.-C.T; Methodology, Y.-J.S; Software, M.-Y.C; Validation, P-Y.Y, J.-S.C and Y.-C.C; Formal Analysis, J.-S.C and Y.-J.S; Investigation, J.-S.C.; Resources, M.-Y.C; Data Curation, J.-S.C and Y.-J.S; Writing-Original Draft Preparation, H.-C.T, M.-Y.C and Y.-J.S; Writing-Review & Editing, P.-Y.Y, T.-Y.H and B.-M.H; Visualization, B.-M.H; Supervision, B.-M.H, P-Y.Y, H.-C.T and J.-S.C; Project Administration, B.-M.H and H.-C.T; Funding Acquisition, B.-M.H, M.-Y.C, P-Y.Y and H.-C.T.

Funding

This research was funded by the Ministry of Science and Technology of Taiwan (MOST 106-2116-M-194-013), the Centers for Disease Control, Taiwan, R.O.C. (MOHW105-CDC-C-114-112601 and 106-CDC-C-114-122601), the Buddhist Tzu Chi Hospital, R.O.C., Show Chwan Health Care System and Cheng Hsin General Hospital (TCRD106-37, RD107023, CHGH106-01). This research was also supported by the Center for Innovative Research on Aging Society (CIRAS) from The Featured Areas Research Center Program within the framework of the Higher Education Sprout Project by the Ministry of Education (MOE) in Taiwan.

Conflicts of Interest

The authors declare that they have no conflict of interest.

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Water 10 01374 g001
Figure 1. Sampling locations on the Puzi River in this study (P indicates the distribution of Acinetobacter baumannii; numbers indicate the number of strains detected).
Figure 1. Sampling locations on the Puzi River in this study (P indicates the distribution of Acinetobacter baumannii; numbers indicate the number of strains detected).
Water 10 01374 g001
Water 10 01374 g002
Figure 2. Sampling locations of wastewater surrounding the Puzi River basin in this study (P indicates the distribution of Acinetobacter baumannii; numbers indicate the number of isolates detected).
Figure 2. Sampling locations of wastewater surrounding the Puzi River basin in this study (P indicates the distribution of Acinetobacter baumannii; numbers indicate the number of isolates detected).
Water 10 01374 g002
Water 10 01374 g003
Figure 3. Amplification clustering patterns of Acinetobacter baumannii (AB) by enterobacterial repetitive intergenic consensus PCR (ERIC-PCR).
Figure 3. Amplification clustering patterns of Acinetobacter baumannii (AB) by enterobacterial repetitive intergenic consensus PCR (ERIC-PCR).
Water 10 01374 g003
Table 1. Detection rate of Acinetobacter baumannii from the Puzi River per annum.
Table 1. Detection rate of Acinetobacter baumannii from the Puzi River per annum.
Sampling DatePositive SamplesTotal SamplesDetection Rate
14 May52420.8%
14 June0240
14 July32412.5%
14 August1244.2%
14 September2248.3%
14 October0240
14 November0240
14 December0240
15 January0240
15 February0240
15 March0240
15 April0240
Total112883.8%
Table 2. Detection rate of Acinetobacter baumannii for different sampling areas.
Table 2. Detection rate of Acinetobacter baumannii for different sampling areas.
LocationSitesPositive SamplesTotal SamplesDetection Rate
Puzi RiverArea A (PR01-PR12)5965.2%
Area B (PR14-PR25)4964.2%
Area C (PR26-PR34)2962.1%
Channels and tributariesLivestock wastewater channels31421.4%
Household wastewater channels030%
Puzi River tributaries21315.4%
Table 3. Antibiotic susceptibility of environmental Acinetobacter baumannii isolates as determined by Kirby-Bauer disk diffusion tests.
Table 3. Antibiotic susceptibility of environmental Acinetobacter baumannii isolates as determined by Kirby-Bauer disk diffusion tests.
Antibiotics Resistance PhenotypeNumberResistantIntermediateSusceptible
Ciprofloxacin200020 (100%)
Cefepime200020 (100%)
Gentamicin200020 (100%)
Imipenem200020 (100%)
Ampicillin-sulbactam200020 (100%)
Sulphamethoxazole/Trimethoprim2004 (20%)16 (80%)
Tetracycline201 (5%)2 (10%)17 (85%)
Table 4. Antibiotic susceptibility of different Acinetobacter baumannii isolates from the aquatic environment.
Table 4. Antibiotic susceptibility of different Acinetobacter baumannii isolates from the aquatic environment.
No.Code of StrainsAntibiotics Resistance Phenotype
CIPFEPGISAMSXTT
1ATCC-16906SSSSSRI
2A. baumannii-PR07-0531SSSSSIS
3A. baumannii-PR09-0531SSSSSIS
4A. baumannii-PR21-0511SSSSSII
5A. baumannii-PR23-0521SSSSSIS
6A. baumannii-PR31-0511SSSSSSS
7A. baumannii-PR07-0711SSSSSSS
8A. baumannii-PR07-0721SSSSSSS
9A. baumannii-PR22-0711SSSSSSS
10A. baumannii-PR26-0721SSSSSSS
11A. baumannii-PR25-0811SSSSSSS
12A. baumannii-PR25-0821SSSSSSS
13A. baumannii-PR05-0911SSSSSSS
14A. baumannii-PR05-0912SSSSSSS
15A. baumannii-PR12-0911SSSSSSS
16A. baumannii-PR12-0912SSSSSSS
17A. baumannii-GI-IM0511SSSSSSS
18A. baumannii-GI-IM0611SSSSSSI
19A. baumannii-GI-G04311SSSSSSS
20A. baumannii-GI-G08211SSSSSSS
21A. baumannii-GI-G11511SSSSSSR
Notes: CIP: Ciprofloxacin, FEP: Cefepime, GEN: Gentamicin, IPM: Imipenem, SAM: Ampicillin-sulbactam, SXT: Sulphamethoxazole/Trimethoprim, T: Tetracycline, R: Resistant, I: Intermediately resistant, S: Susceptible.

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Tsai, H.-C.; Chou, M.-Y.; Shih, Y.-J.; Huang, T.-Y.; Yang, P.-Y.; Chiu, Y.-C.; Chen, J.-S.; Hsu, B.-M. Distribution and Genotyping of Aquatic Acinetobacter baumannii Strains Isolated from the Puzi River and Its Tributaries Near Areas of Livestock Farming. Water 2018, 10, 1374. https://doi.org/10.3390/w10101374

AMA Style

Tsai H-C, Chou M-Y, Shih Y-J, Huang T-Y, Yang P-Y, Chiu Y-C, Chen J-S, Hsu B-M. Distribution and Genotyping of Aquatic Acinetobacter baumannii Strains Isolated from the Puzi River and Its Tributaries Near Areas of Livestock Farming. Water. 2018; 10(10):1374. https://doi.org/10.3390/w10101374

Chicago/Turabian Style

Tsai, Hsin-Chi, Ming-Yuan Chou, Yi-Jia Shih, Tung-Yi Huang, Pei-Yu Yang, Yi-Chou Chiu, Jung-Sheng Chen, and Bing-Mu Hsu. 2018. "Distribution and Genotyping of Aquatic Acinetobacter baumannii Strains Isolated from the Puzi River and Its Tributaries Near Areas of Livestock Farming" Water 10, no. 10: 1374. https://doi.org/10.3390/w10101374

APA Style

Tsai, H.-C., Chou, M.-Y., Shih, Y.-J., Huang, T.-Y., Yang, P.-Y., Chiu, Y.-C., Chen, J.-S., & Hsu, B.-M. (2018). Distribution and Genotyping of Aquatic Acinetobacter baumannii Strains Isolated from the Puzi River and Its Tributaries Near Areas of Livestock Farming. Water, 10(10), 1374. https://doi.org/10.3390/w10101374

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