Next Article in Journal
Preventing Multidrug-Resistant Bacterial Transmission in the Intensive Care Unit with a Comprehensive Approach: A Policymaking Manual
Previous Article in Journal
Chemical Composition of Ailanthus altissima (Mill.) Swingle Methanolic Leaf Extracts and Assessment of Their Antibacterial Activity through Oxidative Stress Induction
 
 
Search for Articles:
Title / Keyword
Author / Affiliation / Email
Journal
Article Type
 
 
Advanced Search
 
Section
Special Issue
Volume
Issue
Number
Page
 
Journals
Antibiotics
Volume 12
Issue 8
10.3390/antibiotics12081254
antibiotics-logo
Submit to this Journal Review for this Journal Propose a Special Issue
► Article Menu

Article Menu

share Share announcement Help format_quote Cite question_answer Discuss in SciProfiles thumb_up
...
Endorse textsms
...
Comment
first_page
settings
Order Article Reprints
Font Type:
Arial Georgia Verdana
Font Size:
Aa Aa Aa
Line Spacing:
Column Width:
Background:
Article

Effects of Florfenicol on nirS-Type Denitrification Community Structure of Sediments in an Aquatic Microcosm Model

by
Tengyue Zhang
1,2,†,
Junying Sun
3,†,
Jinju Peng
1,
Yuexia Ding
1,
Yang Li
1,
Haotian Ma
1,
Mengbo Yu
1 and
Yi Ma
1,*
1
Department of Veterinary Medicine, College of Coastal Agricultural Sciences, Guangdong Ocean University, Zhanjiang 524088, China
2
College of Veterinary Medicine, Yangzhou University, Yangzhou 225000, China
3
Institute of Animal Health, Guangdong Academy of Agricultural Sciences, Guangzhou 510000, China
*
Author to whom correspondence should be addressed.
†
These authors contributed equally to this work.
Antibiotics 2023, 12(8), 1254; https://doi.org/10.3390/antibiotics12081254
Submission received: 24 June 2023 / Revised: 22 July 2023 / Accepted: 26 July 2023 / Published: 30 July 2023
Browse Figures
Review Reports Versions Notes

Abstract

:
Florfenicol is one of the most widely used antibiotics in aquaculture and veterinary clinics because of its low side effects and strong bactericidal effect. A total of 45~60% of florfenicol is not absorbed by the animal body and accumulates in the aquatic environment through a variety of pathways, which affects denitrification. Indoor aquatic microcosm models were constructed and sediment samples were collected at different florfenicol concentrations (0.1, 1, 10, and 100 mg/L) on days 0, 7, 30, and 60 to extract the microbial genome DNA and determine the water properties. qPCR and amplicon sequencing were used to study the dynamic changes in the nirS gene and nirS-type denitrification community structure, diversity, and abundance, respectively. The results showed that high florfenicol stress influenced the sediment’s physicochemical properties, reducing conductivity, alkaline dissolved nitrogen, and organic matter content. In addition, the abundance of nirS, a functional denitrification gene, increased obviously with increased florfenicol concentrations but decreased the diversity of nirS-type denitrification microorganisms. Proteobacteria was the dominant denitrifying phylum in the sediment. Our study provides a scientific basis for the rational use of florfenicol in aquaculture to maintain a healthy and stable microecological environment and also provides a preliminary understanding of the response characteristics of water denitrifying microorganisms to florfenicol exposure.

1. Introduction

The use of antibiotics in livestock farming will continue to grow as the scale of intensive farming develops and expands, and the dependence on antibiotics in the farming process is becoming more severe. Global antibiotic consumption is expected to increase by 67% from 2010 to 2030 [1]. The annual usage of antibiotics in livestock farming globally is estimated to be 99,502 tons in 2020 and is expected to increase by 8% to 107,472 tons by 2030 [2]. However, only limited amounts of antibiotics are absorbed and utilized by human and animal organisms; most of the antibiotics are excreted in urine or feces [3,4]. The excreted antibiotics are released into the environment through direct or indirect ways and eventually pool in the aquatic environment. At present, antibiotic residues have been detected in various environments, including lakes, oceans, soils, sediments, farming wastewater, groundwater, surface water, and even drinking water. The detected concentrations of antibiotics were mostly in the ng or μg range in the environment, but the direct discharge of untreated livestock manure and farm wastewater can even lead to detected concentrations of antibiotics at the mg level in the surrounding environment, which seriously destabilizes the ecological environment [5,6,7]. In Korea, florfenicol was detected in the mainstream of the Han River at a concentration of 340 ng/L [8]. In Brazil and France, the highest concentrations of florfenicol have been reported in surface waters in the amount of 430 and 930 ng/L, respectively [9,10]. The residual concentration of florfenicol was as high as 11 mg/L in the waters around the Dalian Bay aquacultural farms in China [11]. In addition, Wang et al. examined the antibiotic content of children’s urine in Shanghai and found that florfenicol showed a frequency of detection of 32.3%, with a concentration of 67.71 μg/L [12].
Denitrification is an enzymatic reduction reaction mediated by microorganisms that use NO3− or NO2− as substrates to eventually produce N2O or N2, resulting in denitrification, which can occur in anaerobic, anoxic, and aerobic conditions [13,14,15]. Denitrification is the most important denitrification mechanism in freshwater lake systems, and its denitrification efficiency is much higher than anaerobic ammonia oxidation [16]. Nitrite reductases, coded by nirK and nirS genes together, are rate-limiting enzymes of the denitrification process that have the same function, but their subunit structures and numbers, catalytic sites, cofactors, and phylogenetic relationships are different [17]. Related studies have shown that nirS-type denitrification communities and nirK-type denitrification communities have different ecological niche preferences and response mechanisms to environmental factors [18,19]. Wang et al. [20] found that nirK-type denitrification communities have higher richness and diversity in soils [21]. Shi et al. [22] found that the nirS-type denitrification communities exhibited markedly more richness and diversity than nirK-type denitrification communities in the sediments of the southern bay of China. Some other studies have shown a correlation between antibiotic resistance genes and nitrogen cycling under antibiotic stress [23]. Antibiotics can inhibit nitrate and nitrite reduction by affecting key genes for denitrification [24], reducing functional enzyme activity [25], impeding the growth of denitrification bacteria [26,27], and altering the structure and diversity of the microbial community [28].
Florfenicol is one of the widely used antibiotics in the aquaculture industry, with annual usage once exceeding 10,000 tons [29,30], but there are only limited reports about the effects of florfenicol on the denitrification microbial community structure in aquatic ecosystems. In this study, the indoor construction of aquatic microcosm models was used to simulate aquatic ecosystems. The effects of florfenicol stress on the nirS-type denitrification microbial community structure in sediments were investigated by qPCR and high-throughput sequencing techniques to provide a preliminary understanding of the response characteristics of nirS-type denitrification microbes in sediment to florfenicol stress; to provide an important basis for an in-depth understanding of the effects of florfenicol on the environmental microbial community; and to provide the basis for better assessment and management regarding the environmental risk of florfenicol in the environment.

2. Results

2.1. Effects of Florfenicol Stress on Physicochemical Properties in Sediments

The physicochemical properties of the sediments are shown in Table 1. Sediment samples were all weakly alkaline, and florfenicol had no obvious effect on their pH. The conductivity of the sediment gradually decreased with increasing florfenicol concentration in the experimental groups. In control and low-concentration experimental groups, conductivity increased at 7 and 30 days followed by a decrease at 60 days in sediments. The conductivity under high-drug-concentration stress decreased at both 7 and 30 days, and the lowest value was reached at 30 days in the S4 group, with a marked rebound at 60 days. This indicates that high florfenicol concentration decreases the conductivity of sediments, and the conductivity gradually recovers with time. The alkaline nitrogen content of sediments gradually increased from 0 to 30 days; at 60 days, it increased in low-concentration experimental groups and decreased in control and high-concentration experimental groups. The organic matter content in the control groups showed an increasing trend; that in the experimental groups showed a decreasing trend, and at 60 days, the organic matter content was lower than at day 0 in all experimental groups.

2.2. Effects of Florfenicol on nirS Gene Abundance

The dynamic changes in nirS, the coding gene for nitrite reductase, in sediments were detected by qPCR, and results are shown in Figure 1. The absolute abundance of the nirS gene ranged from 3.59 × 104 to 6.29 × 105 copies/μL in sediments. In control groups (0 d and 0 mg/L), nirS gene abundance did not change markedly over time. In experimental groups, nirS gene abundance increased with increased drug concentration and time and reached the maximum nirS gene abundance at 60 days.

2.3. Effect of Florfenicol on nirS-Type Denitrification Community Structure

After the quality optimization of the original data, the number of valid sequences obtained in sediments was 91,816~189,063. After OTU cluster analysis, the number of OTUs in each sample ranged from 2420 to 5389, with an average of 3902 OTUs per sample. The 20 samples were divided into different groups according to the sampling time and florfenicol addition concentration, and then OTU clustering analysis was performed. According to the OTU cluster analysis results, a Venn diagram was drawn. The sampling time obviously decreases the number of co-OTUs in sediments; as shown in Figure 2, the number of co-OTUs in samples at 0 days was 1868; the number of co-OTUs in samples at 7, 30, and 60 days decreased sequentially to 1464, 686, and 580, respectively.
The microbial community diversity indices mainly include the Shannon and Simpson indices, and the richness indices mainly include the Chao1 and ACE indices. Larger indices represent a greater total species number and higher community diversity. Goods coverage is the sequencing depth index, which indicates the coverage of each sample library, whose higher values indicate the lower probability that sequences are not detected in the samples. As shown in Table 2, each sample had a Goods coverage index greater than 0.94, indicating that the nirS gene sequence detection coverage was high in samples, which could reflect the nirS-type denitrification microorganisms in sediments more realistically and comprehensively. At 7 days, florfenicol stress did not affect the Shannon index for the denitrification microbial community; at 30 days, the Shannon index decreased in all experimental groups, and it decreased with increased florfenicol concentration at 60 days. The richness index of the denitrification microbial community showed an increasing trend at 7 days and decreased obviously at 30 days; at 60 days, the richness index decreased continuously in high-concentration experimental groups. OTUs numbers showed a similar trend to the richness index, and the OTUs number decreased by 30.18% and 42.43% in high-concentration experimental groups at 60 days, respectively.
The nirS-type denitrification microbial community composition of each sample was statistical under different species’ classification levels. The identified species were classified into 7 phyla 12 classes, 18 orders, 21 families, 41 genera, and 81 species. The relative abundance of each species in the denitrifying communities was calculated, with the relative abundance of unclassified species ranging from 74.35% to 87.07%. At the phylum level, the relative abundance of Proteobacteria ranged from 5.10% to 24.49% and mainly included Betaproteobacteria, Alphaproteobacteria, and Gammaproteobacteria, which were the absolute dominant bacteria. The relative abundance of Betaproteobacteria was the highest and the relative abundance of Gammaproteobacteria was the lowest. The top 30 species at the genus level were selected to draw a clustering heat map, and the similarities and differences in species distributions were visualized by their color differences, as shown in Figure 3. Thauera, Azoarcus, Dechloromonas, Acidovorax, Thiobacillus, Comamonas, Pseudomonas, and Rhodanobacter were the dominant bacteria at the genus level, with relative abundance more than 0.5%. Some bacteria showed obvious changes in relative abundance, among which the relative abundance of Thauera in samples S3D60 and S4D60 was only 0.94% and 1.2%, with an obvious decrease compared to the other groups; in sample S4D60, the relative abundance of Azoarcus, Dechloromonas, and Alicycliphilus was 8.93%, 6.15%, and 3.89%, respectively, which clearly increased compared with the other groups. The relative abundance of Marinobacter in S3D60 was 5.62%, but the relative abundance in the other groups was less than 0.3%.

2.4. Beta Diversity

The PCoA (Principal coordinates analysis) and UPGMA (unweighted pair group method with arithmetic mean) clustering methods were used to express the similarity and difference degrees between different samples. As shown in Figure 4, the contributions of PC1 and PC2 principal coordinates to sample differences were 20.45% and 16.96%, respectively, in PCoA. Samples with different sampling times were completely separated, indicating that sampling time was the dominant factor in the degree of variation between samples. The treatment groups with higher florfenicol addition concentrations at 30 and 60 days were the furthest away from the control group, indicating that the nirS-type denitrification microbial community was more different and more influenced by the drug. Similarly, treatment groups with 10 and 100 mg/L florfenicol added concentrations at 30 and 60 days clustered together and were the furthest away from the control group in the cluster analysis. Samples with the same sampling time were clustered together in the cluster analysis. The cluster analysis results were consistent with the dispersion between samples in the PCoA analysis.

2.5. Linkage among Sediment Properties, nirS Gene Abundance, and nirS-Type Denitrification Communities

The top 10 nirS-type denitrification bacteria with higher relative abundance in each sample were selected, and redundancy analysis (RAD) was used to investigate their correlations with sediment properties and nirS gene abundance. The results are shown in Figure 5. Dechloromonas, Marinobacter, and Azoarcus showed clearly positive correlations with nirS genes; Thiobacillus, Thauera, and Rhodanobacter showed clearly negative correlations with nirS genes. Thiobacillus showed the strongest correlation with pH, with a clearly positive correlation. Pseudomonas, Alicycliphilus, Acidovorax, and Comamonas showed clearly positive correlations with organic matter and negative correlations with alkaliolytic nitrogen. Thauera and Rhodanobacter showed positive correlations with electrical conductivity and alkaliolytic nitrogen.

3. Discussion

Antibiotic residues in the environment cause widespread dissemination and prevalence of antibiotic resistance genes and also affect the nitrogen cycle, especially the denitrification process in aquatic systems, which is important for mitigating nitrate pollution. Some studies have reported that antibiotics affect or inhibit the denitrification process to varying degrees [31,32,33], inhibiting the activity of key functional enzymes of denitrification microorganisms [32]. However, it has also been reported that the antibiotic negative effects decrease to a degree over time and a gradual adaptation to antibiotic stress can be observed overall [33,34]. Wu et al. [35] found that denitrification functional gene levels were reduced under sulfadimethoxine stress and that Pseudomonas was sufficiently enriched as a major antibiotic resistance genes carrier. Sun et al. [36] found that denitrification significantly reduced antibiotic levels and antibiotic resistance gene abundance, and there was a significant negative correlation between denitrification functional genes and antibiotic resistance genes. However, some studies also reported that trace and low concentrations of antibiotics (spiramycin, streptomycin, hygromycin, and ciprofloxacin) did not significantly inhibit denitrification efficiency but resulted in reduced abundance of related bacterial genera and enrichment of antibiotic resistance genes [37,38]. Some antibiotics also promoted the proliferation of denitrifying bacteria and partial nitrification and denitrification to improve nitrogen pollution [39,40]. Gonzalez et al. [41] found that norfloxacin and sulfamethoxazole significantly increased the expression of denitrification genes and antibiotic resistance genes. Li et al. [42] and Huang et al. [43] found that tetracycline promoted the growth of denitrifying bacteria. Roose-Amsaleg et al. [44] found that tetracycline at therapeutic concentrations (10 mg/L) altered the community structure of denitrifying bacteria but did not affect the denitrification process, while Zhang et al. [45] observed that the accumulation of nitrate and nitrite was 4.21 and 10 times higher, respectively, than the control after exposure to 2 mg/kg tetracycline in the same sediment. An et al. [46] found that an increased concentration of sulfamethoxazole from 0.1 to 10 mg/L significantly inhibited nitrate removal in the wastewater. However, Fan et al. [47] found that low concentrations (<0.2 mg/L) of sulfamethoxazole led to a decrease in nitrate removal in earlier stages, but higher concentrations (0.4 to 20 mg/L) of sulfamethoxazole had no further inhibitory effect. Obviously, there are different conclusions on the effects of antibiotics on denitrification and even some contradictory conclusions. This may be related to the composition of denitrification microorganisms and the sensitivity of different denitrification bacteria to antibiotics.
In our study, high florfenicol stress influenced sediment physicochemical properties, reducing conductivity, alkaline-dissolved nitrogen, and organic matter content. In addition, the abundance of nirS, a functional denitrification gene, increased obviously with increased florfenicol concentrations but decreased the diversity of nirS-type denitrification microorganisms. Several studies have shown that florfenicol slightly promotes nitrite reductase encoding gene abundance for a short period of time [32,48]. The same phenomenon was found in our previous study: the florfenicol addition to aquatic microcosms suppressed the aquatic denitrifying microbial community diversity but increased the nirS gene abundance, and in addition, the treatment group with lower florfenicol addition induced a marked increase in florfenicol-resistant genes in aquatic environments [31,49]. This may be due to the combined effect of drug and time that some strains carrying nirS genes acquired florfenicol resistance genes and became dominant bacteria under florfenicol stress. However, functional gene abundance only indicates the potential for functional activity, and the actual role may be limited by mRNA expression and post-transcriptional modifications of functional genes in the environment [50]. Certain bacteria can adapt to poorer survival environments by increasing their transcriptional activity [51]. It was found that functional genes for denitrification processes in marine and estuarine environments have low, and in some cases undetectable, transcriptional abundance [52,53]. Exposure to high antibiotic concentrations may stimulate the transfer and replication of plasmids carrying resistance genes in denitrifying microbial communities, causing resistance gene abundance to increase; in addition, denitrifying bacteria may develop resistance to antibiotics to adapt to antibiotic-induced stress.

4. Materials and Methods

4.1. Reagents

The lake surface water (1–10 cm) and lake surface sediments (1–10 cm) in Guangdong Ocean University (Zhanjiang, China) were collected, and the debris was removed to construct an aquatic microcosm. Florfenicol (13021322) was purchased from North China Pharmaceutical Co., Ltd. (Shijiazhuang, China). The Soil DNA Kit (D5625) and MicroElute Gel Extraction Kit (D6294) were purchased from Omega Bio-Tek Company (Guangzhou, China). The TIANprep Midi Plasmid Kit (DP106-02) was purchased from Tiangen Biochemical Technology Co., Ltd. (Beijing, China). The pMDTM19-T Vector Cloning Kit (6013) was purchased from Bao Bioengineering Co., Ltd. (Dalian, China). The ChamQ Universal SYBR qPCR Master Mix (Q711- 02) was purchased from Nanjing Novizan Biotechnology Co., Ltd. (Nanjing, China). The DH5α competent cells (B528413), Real-time PCR Plates, 96-Well Transparent, Non Skirted (F603101), and primers were purchased from Sangon Bioengineering Co., Ltd. (Shanghai, China).

4.2. Aquatic Mesocosm Experiment Design and Sampling

The mesocosm experiment was constructed to simulate the aquatic ecosystem. Surface water (1–10 cm) and surface sediments (1–10 cm) were collected from lakes at the Guangdong Ocean University (Zhanjiang, China), larger stones and other debris were removed, and the samples were divided into transparent plastic boxes (50 × 40 × 30 cm). Each plastic box contained 30 L of lake water and 10 cm of sediment, and the depth of water was 15 cm. The constructed aquatic mesosystems were stabilized at room temperature (25 ± 3 °C) for 3 days. Florfenicol solution was added so that the concentration of florfenicol in the water column was 0 (control group), 0.1, 1, 10, and 100 mg/L. Among them, 0 mg/L was the control group, 0.1 and 1 mg/L were the low-concentration experimental groups, and 10 and 100 mg/L were the high-concentration experimental groups. Sediment samples (numbered S0 to S4) were collected on days 0, 7, 30, and 60 (D0, D7, D30, and D60; among them, D0 was the control group). The in vitro bacteriostatic effect of the configured florfenicol solution was tested using the microbroth twofold dilution method, and the MIC of florfenicol against Escherichia coli was found to be 8 μg/mL, which ensured that the solution had a significant bacteriostatic effect. The experiment had 5 groups with 3 replicates each. Each group of three samples was divided into two parts, one of which was used for the determination of physical and chemical properties; the other part was used for DNA extraction, and the DNA was mixed before being sent for sequencing.

4.3. Analysis of Sample Physical and Chemical Properties

Several experiments were performed to assess the physiochemical characteristics of the samples. For example, sediment pH was measured using a pH meter (PHS-3B, Leici Shanghai, Shanghai, China ) with a water-to-soil ratio of 2.5:1; sediment conductivity was measured using a conductivity meter (DDS-307A, Leici Shanghai) with a water-to-soil ratio of 5:1; the volumetric method (using potassium dichromate) was used to measure the amount of organic matter; and alkaline hydrolysis was used to determine the amount of alkali-hydrolyzable nitrogen. Each sample was analyzed in triplicate.

4.4. DNA Extraction and qPCR

According to the manufacturer’s instructions, genomic DNA was extracted from sediment samples using the soil DNA kit (Omega Bio-Tek, Norcross, GA, USA). The concentration and purity of the extracted DNA were assessed using a nanodrop UV–vis spectrophotometer. Three DNA samples were extracted from each group for analysis. Based on previous work, the SYBR-primer method was employed with the CFX Connect Real-Time System instrument (BIO-RAD, Hercules, CA, USA) to determine the abundance of the nirS gene. The denitrifying bacterial nirS gene was amplified using the primer pair CD3AF/R3CDR. The qPCR reaction system was as follows: 10 µL SYBR, 1 µL DNA template, 1 µL upstream and downstream primers (10 mol·L−1) each, and 8 µL ddH2O. The qPCR reaction program was as follows: 94 °C, 5 min; 94 °C for 30 s, 58 °C for 30 s, 72 °C for 30 s, 39 cycles. The absolute abundance of nirS genes was calculated according to the method of Zhang et al. [31].

4.5. Amplicon Sequencing of nirS Gene and Bioinformatics Processing

The DNA samples from each of the three replicates were combined into the mixed sample and sent to Jinweizhi (Suzhou, China) for Illumina MiSeq paired-end sequencing of the nirS gene amplicon regions. The nirS gene was amplified for sequencing analysis using the same primer pairs as qPCR. The high-throughput sequencing raw data were optimized using QIIME 1.9.1 by splicing overlapping regions at the ends of the sequences, removing sequences that were shorter than 200 bp, and removing chimeric sequences to produce valid data. An operational taxonomic unit (OTU) cluster analysis was carried out on the basis of a 97% similarity. The species taxonomic annotation was completed using the NCBI database. Based on OTU analysis, results were obtained using the method of random sampling; sample sequences were flat, and we calculated the Shannon and Chao1 alpha diversity indices, community species abundance, and diversity. The diversity index was examined using QIIME 1.9.1 software and R language.

4.6. Statistical Analysis

Excel 2016 was used to analyze the nirS gene abundance, QIIME 1.9.1 software was used to perform the α diversity index analysis, R language was used for β diversity analysis, and the correlation between environmental factors and community structure was examined using CANOCO 5.0 software.

5. Conclusions

In this study, Proteobacteria was the dominant denitrifying phylum under florfenicol stress in sediment. High florfenicol stress influenced sediment physicochemical properties, reducing conductivity, alkaline-dissolved nitrogen, and organic matter content. In addition, the abundance of nirS, a functional denitrification gene, increased obviously with increased florfenicol concentrations but decreased the diversity of nirS-type denitrification microorganisms. Proteobacteria was the dominant denitrifying phylum in sediment.

Author Contributions

Funding acquisition, Y.M.; investigation, T.Z. and Y.D.; methodology, T.Z. and J.S.; project administration, Y.D. and J.P.; software, H.M. and Y.L.; data curation, M.Y. and J.P.; visualization, J.P.; supervision, Y.M.; writing—original draft, T.Z.; writing—review and editing, J.P. and J.S. All authors have read and agreed to the published version of the manuscript.

Funding

This research was funded by the Natural Science Foundation of Guangdong Province, China (2023A1515012181); the Zhanjiang Science and Technology Bureau 2021 Provincial Science and Technology Special Funds (“Big Special + Task List”) Competitive Allocation Project (2021A05231); and the Science and Technology Planning Project of Guangzhou city, China (202002030456, 20212100050).

Institutional Review Board Statement

Not applicable.

Informed Consent Statement

Not applicable.

Data Availability Statement

The 16S rDNA sequencing data have been uploaded to the repository (National Center for Biotechnology Information, NCBI), which can be found at the link http://www.ncbi.nlm.nih.gov/bioproject/986876, and the Accession no. is PRJNA986876, accessed on 23 July 2023.

Conflicts of Interest

The authors declare no conflict of interest.

References

  1. Van Boeckel, T.P.; Brower, C.; Gilbert, M.; Grenfell, B.T.; Levin, S.A.; Robinson, T.P.; Teillant, A.; Laxminarayan, R. Global trends in antimicrobial use in food animals. Proc. Natl. Acad. Sci. USA 2015, 112, 5649–5654. [Google Scholar] [CrossRef] [PubMed]
  2. Gil, J. Antimicrobial use in livestock farming. Nat. Food 2023, 4, 138. [Google Scholar] [CrossRef]
  3. Liu, P.X.; Wang, X.; Feng, L. Occurrence, resources, and risks of antibiotics in aquatic environmental: A review. Environ. Eng. 2020, 38, 36–42. (In Chinese) [Google Scholar]
  4. Liu, J.Z.; Fung, K.F.; Chen, Z.L.; Zeng, Z.L.; Zhang, J. Pharmacokinetics of florfenicol in healthy pigs and in pigs experimentally infected with Actinobacillus pleuropneumoniae. Antimicrob. Agents Chemother. 2003, 47, 820–823. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  5. Gu, J.Y.; Chen, C.Y.; Huang, X.Y.; Mo, J.C.; Xie, Q.L.; Zeng, Q.Y. Occurrence and risk assessment of tetracycline antibiotics in soils and vegetables from vegetable fields in Pearl River Delta, South China. Sci. Total Environ. 2021, 776, 145959. [Google Scholar] [CrossRef]
  6. Lyu, J.; Yang, L.S.; Zhang, L.; Ye, B.X.; Wang, L. Antibiotics in soil and water in China–a systematic review and source analysis. Environ. Pollut. 2020, 266, 115147. [Google Scholar] [CrossRef] [PubMed]
  7. Pan, Z.; Yang, S.D.; Zhao, L.X.; Li, X.J.; Weng, L.P.; Sun, Y.; Li, Y.T. Temporal and spatial variability of antibiotics in agricultural soils from Huang-Huai-Hai Plain, northern China. Chemosphere 2021, 272, 29803. [Google Scholar] [CrossRef]
  8. Kim, Y.; Lee, K.B.; Choi, K. Effect of runoff discharge on the environmental levels of 13 veterinary antibiotics: A case study of Han River and Kyungahn Stream, South Korea. Mar. Pollut. Bull. 2016, 107, 347–354. [Google Scholar] [CrossRef]
  9. Monteiro, S.H.; Francisco, J.G.; Andrade, G.C.; Botelho, R.G.; Figueiredo, L.A.; Tornisielo, V.L. Study of spatial and temporal distribution of antimicrobial in water and sediments from caging fish farms by on-line SPE-LC-MS/MS. J. Environ. Sci. Health Part B 2016, 51, 634–643. [Google Scholar] [CrossRef]
  10. Charuaud, L.; Jarde, E.; Jaffrezic, A.; Liotaud, M.; Goyat, Q.; Mercier, F.; Le Bot, B. Veterinary pharmaceutical residues in water resources and tap water in an intensive husbandry area in France. Sci. Total Environ. 2019, 664, 605–615. [Google Scholar] [CrossRef] [Green Version]
  11. Na, G.S.; Fang, X.D.; Cai, Y.Q.; Ge, L.K.; Zong, H.M.; Yuan, X.T.; Yao, Z.W.; Zhang, Z.F. Occurrence, distribution, and bioaccumulation of antibiotics in coastal environment of Dalian, China. Mar. Pollut. Bull. 2013, 69, 233–237. [Google Scholar] [CrossRef]
  12. Wang, H.; Wang, N.; Wang, B.; Fang, H.; Fu, C.W.; Tang, C.X.; Jiang, F.; Zhou, Y.; He, G.S.; Zhao, Q.; et al. Antibiotics detected in urines and adipogenesis in school children. Environ. Int. 2016, 89, 204–211. [Google Scholar] [CrossRef]
  13. Huang, C.; Liu, Q.; Li, Z.L.; Ma, X.D.; Hou, Y.N.; Ren, N.Q.; Wang, A.J. Relationship between functional bacteria in a denitrification desulfurization system under autotrophic, heterotrophic, and mixotrophic conditions. Water Res. 2021, 188, 16526. [Google Scholar] [CrossRef]
  14. Tan, P. Study on Denitrification Performance and Key Enzyme Functional Genes of an Aerobic Denitrifier, Pseudomonas stutzeri XL-2. Master’s Thesis, Chongqing University, Chongqing, China, 2017. (In Chinese). [Google Scholar]
  15. Zhou, X.T.; Zhao, L.; Wang, X.; Wang, X.C.; Wei, J.; Fang, Z.; Li, S.W.; Rong, X.S.; Luo, Z.J.; Liang, Z.S.; et al. Organic and inorganic nitrogen removals by an ureolytic heterotrophic nitrification and aerobic denitrification strain Acinetobacter sp.Z1: Elucidatingits physiological characteristics and metabolic mechanisms. Bioresour. Technol. 2022, 362, 127792. [Google Scholar] [CrossRef] [PubMed]
  16. Dong, L.F.; Sobey, M.N.; Smith, C.J.; Rusmana, I.; Phillips, W.; Stott, A.; Osborn, A.M.; Nedwell, D.B. Dissimilatory reduction of nitrate to ammonium, not denitrification or anammox, dominates benthic nitrate reduction in tropical estuaries. Limnol. Oceanogr. 2011, 56, 279–291. [Google Scholar] [CrossRef]
  17. Wang, B.R.; Wang, X.; Wang, W.B.; Tang, D.S. Cu-NiR and cd-1-NiR: Advances in two kinds of denitrifying nitrite reductase. Plant Sci. J. 2021, 39, 324–334. (In Chinese) [Google Scholar]
  18. Smith, J.M.; Ogram, A. Genetic and functional variation in denitrifier populations along a short-term restoration chronosequence. App. Environ. Microb. 2008, 74, 5615–5620. [Google Scholar] [CrossRef] [Green Version]
  19. Yi, N.; Gao, Y.; Zhang, Z.H.; Wang, Y.; Liu, X.H.; Zhang, L.; Yan, S.H. Response of spatial patterns of denitrifying bacteria communities to water properties in the stream inlets at Dianchi Lake, China. Int. J. Genom. 2015, 2015, 572121. [Google Scholar] [CrossRef] [Green Version]
  20. Wang, Y.; Uchida, Y.; Shimomura, Y.; Akiyama, H.; Hayatsu, M. Responses of denitrifying bacterial communities to short-term waterlogging of soils. Sci. Rep. 2017, 7, 803. [Google Scholar] [CrossRef] [Green Version]
  21. Yang, Y.D.; Hu, Y.G.; Wang, Z.M.; Zeng, Z.H. Variations of the nirS-, nirK-, and nosZ-denitrifying bacterial communities in a northern Chinese soil as affected by different long-term irrigation regimes. Environ. Sci. Pollut. R. 2018, 25, 14057–14067. [Google Scholar] [CrossRef]
  22. Shi, R.J.; Xu, S.M.; Qi, Z.H.; Huang, H.H.; Liang, Q.Y. Seasonal patterns and environmental drivers of nirS- and nirK-encoding denitrifiers in sediments of Daya Bay, China. Oceanologia 2019, 61, 308–320. [Google Scholar] [CrossRef]
  23. Tong, Y.D.; Wang, M.Z.; Peñuelas, J.; Liu, X.Y.; Paerl, H.W.; Elser, J.J.; Sardans, J.; Couture, R.M.; Larssen, T.; Hu, H.Y. Improvement in municipal wastewater treatment alters lake nitrogen to phosphorus ratios in populated regions. Proc. Natl. Acad. Sci. USA 2020, 117, 11566–11572. [Google Scholar] [CrossRef] [PubMed]
  24. Gui, M.; Chen, Q.; Ni, J. Effect of sulfamethoxazole on aerobic denitrification by strain Pseudomonas stutzeri PCN-1. Bioresour. Technol. 2017, 235, 325–331. [Google Scholar] [CrossRef]
  25. Zou, H.; He, J.T.; Guan, X.Y.; Zhang, Y.Y.; Deng, L.; Li, Y.Q.; Liu, F. Microbial responses underlying the denitrification kinetic shifting exposed to ng/L- and μg/L-level lomefloxacin in groundwater. J. Hazard. Mater. 2021, 417, 126093. [Google Scholar] [CrossRef]
  26. Feng, L.J.; Yang, J.Y.; Yu, H.; Lan, Z.Y.; Ye, X.; Yang, G.F.; Yang, Q.; Zhou, J.H. Response of denitrifying community, denitrification genes and antibiotic resistance genes to oxytetracycline stress in polycaprolactone supported solid-phase denitrification reactor. Bioresour. Technol. 2020, 308, 123274. [Google Scholar] [CrossRef]
  27. Zhang, R.J.; Xu, X.M.; Jia, D.T.; Lyu, Y.T.; Hu, J.R.; Chen, Q.; Sun, W.L. Sediments alleviate the inhibition effects of antibiotics on denitrification: Functional gene, microbial community, and antibiotic resistance gene analysis. Sci. Total Environ. 2022, 804, 150092. [Google Scholar] [CrossRef]
  28. Laverman, A.M.; Cazier, T.; Yan, C.; Roose-Amsaleg, C.; Petit, F.; Garnier, J.; Berthe, T. Exposure to vancomycin causes a shift in the microbial community structure without affecting nitrate reduction rates in river sediments. Environ. Sci. Pollut. Res. 2015, 22, 13702–13709. [Google Scholar] [CrossRef]
  29. Ren, Y.Y.; Han, G.; Zeng, H.; Ma, B. General situation and strategy of the potential safety hazard investigation on aquaculture veterinary drugs and other inputs in China. Chin. Fish. Qual. Stand. 2020, 10, 7–11. (In Chinese) [Google Scholar]
  30. Qiao, M.; Ying, G.G.; Singer, A.C.; Zhu, Y.G. Review of antibiotic resistance in China and its environment. Environ. Int. 2018, 110, 160–172. [Google Scholar] [CrossRef] [Green Version]
  31. Zhang, T.Y.; Ding, Y.X.; Peng, J.J.; Dai, Y.; Luo, S.S.; Liu, W.C.; Ma, Y. Effects of broad-spectrum antibiotic (florfenicol) on resistance genes and bacterial community structure of water and sediments in an aquatic microcosm model. Antibiotics 2022, 11, 1299. [Google Scholar] [CrossRef]
  32. Cydzik-Kwiatkowska, A.; Rusanowska, P.; Zielińska, M.; Bernat, K.; Wojnowska-Baryla, I. Structure of nitrogen-converting communities induced by hydraulic retention time and COD/N ratio in constantly aerated granular sludge reactors treating digester supernatant. Bioresour. Technol. 2014, 154, 162–170. [Google Scholar] [CrossRef]
  33. Cui, P.Y.; Fan, F.L.; Yin, C.; Song, A.L.; Huang, P.R.; Tang, Y.J.; Zhu, P.; Peng, C.; Li, T.Q.; Wakelin, S.A. Long-term organic and inorganic fertilization alters temperature sensitivity of potential N2O emissions and associated microbes. Soil Biol. Biochem. 2016, 93, 131–141. [Google Scholar] [CrossRef]
  34. Chen, Q.Q.; Wu, W.D.; Zhang, Z.Z.; Xu, J.J.; Jin, R.C. Inhibitory effects of sulfamethoxazole on denitrifying granule properties: Short- and long-term tests. Bioresour. Technol. 2017, 233, 391–398. [Google Scholar] [CrossRef] [PubMed]
  35. Wu, D.; Chen, G.; Zhang, X.; Yang, K.; Xie, B. Change in microbial community in landfill refuse contaminated with antibiotics facilitates denitrification more than the increase in ARG over long-term. Sci. Rep. 2017, 7, 41230. [Google Scholar] [CrossRef] [Green Version]
  36. Sun, M.; Ye, M.; Liu, K.; Schwab, A.P.; Liu, M.Q.; Jiao, J.G.; Feng, Y.F.; Wan, J.Z.; Tian, D.; Wu, J.; et al. Dynamic interplay between microbial denitrification and antibiotic resistance under enhanced anoxic denitrification condition in soil. Environ. Pollut. 2017, 222, 583–591. [Google Scholar] [CrossRef]
  37. Lu, Z.Y.; Fu, J.J.; Ma, Y.L.; Jin, R.C.; Fan, N.S. Response of anammox granules to the simultaneous exposure to macrolide and aminoglycoside antibiotics: Linking performance to mechanism. J. Environ. Manag. 2021, 286, 112267. [Google Scholar] [CrossRef]
  38. Gamoń, F.; Banach-Wiśniewska, A.; Kaur, J.J.; Cema, G.; Ziembińska-Buczyńska, A. Microbial response of the anammox process to trace antibiotic concentration. J. Water Process. Eng. 2022, 46, 102607. [Google Scholar] [CrossRef]
  39. Yang, C.; Zhang, H.Y.; Zhu, R.X.; Li, X.; Xi, Y.; Luo, S.; Tan, Z.L.; Chen, Y.W. Microbial community characteristics of shortcut nitrification and denitrification process under antibiotic selective pressure. Chin. J. Appl. Environ. Biol. 2022, 28, 394–400. (In Chinese) [Google Scholar]
  40. Li, T.T.; Liu, C.; Lu, J.; Gaurav, G.K.; Chen, W. Determination of how tetracycline influences nitrogen removal performance, community structure, and functional genes of biofilm systems. J. Taiwan Inst. Chem. Eng. 2020, 106, 99–109. [Google Scholar] [CrossRef]
  41. Gonzalez-Martinez, A.; Margareto, A.; Rodriguez-Sanchez, A.; Pesciaroli, C.; Diaz-Cruz, S.; Barcelo, D.; Vahala, R. Linking the effect of antibiotics on partial-nitritation biofilters: Performance, microbial communities and microbial activities. Front. Microbiol. 2018, 9, 354. [Google Scholar] [CrossRef]
  42. Li, J.Z.; Wu, B.L.; Liu, F.R.; Liu, G.G.; Li, X.K. Treatment of Tetracyclines Antibiotics Pharmaceutical Wastewater by BAF. China Water Wastewater 2022, 38, 24–31. (In Chinese) [Google Scholar]
  43. Huang, M.H.; Zhang, W.; Zheng, Y.; Zhang, W. Correlation among extracellular polymeric substances, tetracycline resistant bacteria and tetracycline resistance genes under trace tetracycline. Chemosphere 2014, 117, 658–662. [Google Scholar] [CrossRef]
  44. Roose-Amsaleg, C.; Yan, C.; Hoang, A.M.; Laverman, A.M. Chronic exposure of river sediments to environmentally relevant levels of tetracycline affects bacterial communities but not denitrification rates. Ecotoxicology 2013, 22, 1467–1478. [Google Scholar] [CrossRef]
  45. Zhang, X.Y.; Han, H.N.; Zheng, X.; Yu, T.; Chen, Y.G. Tetracycline-induced effects on the nitrogen transformations in sediments: Roles of adsorption behavior and bacterial activity. Sci. Total Environ. 2019, 695, 133811. [Google Scholar] [CrossRef]
  46. An, Y.L.; Qin, X.M. Effects of sulfamethoxazole on the denitrifying process in anoxic activated sludge and the responses of denitrifying microorganisms. Water Sci. Tec. 2018, 78, 1228–1236. [Google Scholar] [CrossRef] [Green Version]
  47. Fan, N.S.; Bai, Y.H.; Chen, Q.Q.; Shen, Y.Y.; Huang, B.C.; Jin, R.C. Deciphering the toxic effects of antibiotics on denitrification: Process performance, microbial community and antibiotic resistance genes. J. Environ. Manag. 2020, 262, 110375. [Google Scholar] [CrossRef]
  48. Guo, G.X.; Deng, H.; Qiao, M.; Yao, H.Y.; Zhu, Y.G. Effect of long-term wastewater irrigation on potential denitrification and denitrifying communities in soils at the watershed scale. Environ. Sci. Technol. 2013, 47, 3105–3113. [Google Scholar] [CrossRef]
  49. Zhang, T.; Peng, J.; Dai, Y.; Xie, X.P.; Luo, S.S.; Ding, Y.X.; Ma, Y. Effect of florfenicol on nirS-type denitrifying communities structure of water in an aquatic microcosm model. Front. Vet. Sci. 2023, 10, 1205394. [Google Scholar] [CrossRef]
  50. Kim, H.; Bae, H.S.; Reddy, K.R.; Ogram, A. Distributions, abundances and activities of microbes associated with the nitrogen cycle in riparian and stream sediments of a river tributary. Water Res. 2016, 106, 51–61. [Google Scholar] [CrossRef]
  51. Ishida, Y.; Imai, I.; Miyagaki, T.; Kadota, H. Growth and uptake kinetics of a facultatively oligotrophic bacterium at low nutrient concentrations. Microb. Ecol. 1982, 8, 23–32. [Google Scholar] [CrossRef]
  52. Francis, C.A.; O’Mullan, G.D.; Cornwell, J.C.; Ward, B.B. Transitions in nirS-type denitrifier diversity, community composition, and biogeochemical activity along the chesapeake bay estuary. Front. Microbiol. 2013, 4, 237. [Google Scholar] [CrossRef] [Green Version]
  53. Smith, C.J.; Dong, L.F.; Wilson, J.; Stott, A.; Osborn, A.M.; Nedwell, D.B. Seasonal variation in denitrification and dissimilatory nitrate reduction to ammonia process rates and corresponding key functional genes along an estuarine nitrate Gradient. Front. Microbiol. 2015, 6, 542. [Google Scholar] [CrossRef]
Antibiotics 12 01254 g001 550
Figure 1. Effects of different concentrations of florfenicol on the abundance of nirS genes in sediments.
Figure 1. Effects of different concentrations of florfenicol on the abundance of nirS genes in sediments.
Antibiotics 12 01254 g001
Antibiotics 12 01254 g002 550
Figure 2. Effects of different concentrations of florfenicol on operational taxonomic units (OTUs) of bacteria (Venn diagram) in sediments. Effects of different concentrations of florfenicol on OTUs at 0 days (a), 7 days (b), 30 days (c), and 60 days (d). Different colors of circles represent different samples, and the numbers represent the number of unique OTUs in each sample or the number of common OTUs in all samples.
Figure 2. Effects of different concentrations of florfenicol on operational taxonomic units (OTUs) of bacteria (Venn diagram) in sediments. Effects of different concentrations of florfenicol on OTUs at 0 days (a), 7 days (b), 30 days (c), and 60 days (d). Different colors of circles represent different samples, and the numbers represent the number of unique OTUs in each sample or the number of common OTUs in all samples.
Antibiotics 12 01254 g002
Antibiotics 12 01254 g003 550
Figure 3. Effects of different concentrations of florfenicol on genus-level species abundance on nirS-type denitrification microbes in sediments.
Figure 3. Effects of different concentrations of florfenicol on genus-level species abundance on nirS-type denitrification microbes in sediments.
Antibiotics 12 01254 g003
Antibiotics 12 01254 g004 550
Figure 4. Principal coordinates analysis (PCoA) and unweighted pair group method with arithmetic mean (UPGMA) reveal the degrees of similarity and difference of the nirS-type denitrification microbial community between different sediment samples. (a) The results of the PCoA analysis. (b) The results of the UPGMA analysis.
Figure 4. Principal coordinates analysis (PCoA) and unweighted pair group method with arithmetic mean (UPGMA) reveal the degrees of similarity and difference of the nirS-type denitrification microbial community between different sediment samples. (a) The results of the PCoA analysis. (b) The results of the UPGMA analysis.
Antibiotics 12 01254 g004
Antibiotics 12 01254 g005 550
Figure 5. Correlation analysis between nirS-type denitrification microbial and sediment properties and nirS gene abundance in aquatic microcosm models.
Figure 5. Correlation analysis between nirS-type denitrification microbial and sediment properties and nirS gene abundance in aquatic microcosm models.
Antibiotics 12 01254 g005
Table
Table 1. Physicochemical properties in sediments.
Table 1. Physicochemical properties in sediments.
SamplepHConductivity (μS/cm)Alkaline NitrogenOrganic Matter
(mg/kg)(g/kg)
S0D07.88 ± 0.03208.00 ± 5.29173.42 ± 1.0321.76 ± 0.51
S1D07.99 ± 0.12221.00 ± 2.65187.03 ± 2.2026.46 ± 1.53
S2D07.88 ± 0.03213.00 ± 5.29191.67 ± 12.2130.09 ± 0.57
S3D08.04 ± 0.12204.00 ± 4.00179.68 ± 5.0626.55 ± 0.69
S4D07.64 ± 0.02219.00 ± 2.65196.89 ± 1.5733.41 ± 0.62
S0D77.99 ± 0.04249.00 ± 6.08202.72 ± 1.6624.27 ± 2.92
S1D78.01 ± 0.03256.00 ± 3.61199.67 ± 4.0225.33 ± 2.20
S2D77.81 ± 0.08251.00 ± 5.20223.41 ± 4.7230.43 ± 1.10
S3D77.96 ± 0.05233.00 ± 5.57209.62 ± 4.3927.10 ± 0.56
S4D77.63 ± 0.04202.00 ± 7.94216.16 ± 1.9928.75 ± 1.32
S0D308.03 ± 0.04261.00 ± 9.54313.54 ± 9.1220.76 ± 0.51
S1D308.00 ± 0.03275.00 ± 9.17273.53 ± 6.9924.20 ± 1.48
S2D307.78 ± 0.06274.00 ± 4.36261.63 ± 4.6328.38 ± 0.90
S3D307.97 ± 0.03228.00 ± 3.61267.23 ± 3.6625.49 ± 0.57
S4D307.80 ± 0.04119.00 ± 4.58339.91 ± 4.9830.68 ± 2.18
S0D607.50 ± 0.03215.00 ± 1.73248.44 ± 4.9923.03 ± 1.26
S1D607.64 ± 0.02205.00 ± 9.54300.01 ± 6.8624.13 ± 0.66
S2D607.56 ± 0.05195.10 ± 2.01275.04 ± 2.6529.45 ± 1.16
S3D607.77 ± 0.08170.80 ± 6.58225.58 ± 4.8422.13 ± 0.76
S4D607.68 ± 0.06180.80 ± 4.53268.63 ± 6.0629.66 ± 1.30
Table
Table 2. Alpha diversity index of nirS-type denitrification microbial in sediments.
Table 2. Alpha diversity index of nirS-type denitrification microbial in sediments.
SampleOTUsChao1AceShannonSimpsonGoods Coverage
S0D0459210,24710,98510.691.000.95
S1D04312960110,05510.601.000.96
S2D04020968010,06510.411.000.96
S3D046268946947410.381.000.96
S4D04879971510,41410.521.000.96
S0D7519213,50814,43311.131.000.94
S1D7438910,18010,46110.721.000.96
S2D731615200528810.321.000.98
S3D74678962110,17010.341.000.96
S4D7538911,61112,63810.781.000.95
S0D302420466251909.311.000.98
S1D302636576665519.641.000.97
S2D303374699378209.851.000.97
S3D3041888338915410.201.000.96
S4D303921677374439.911.000.97
S0D603796813990479.670.990.96
S1D602982595262339.711.000.98
S2D603455796286158.730.980.96
S3D603230633969628.290.980.97
S4D602809644771307.120.940.97
Disclaimer/Publisher’s Note: The statements, opinions and data contained in all publications are solely those of the individual author(s) and contributor(s) and not of MDPI and/or the editor(s). MDPI and/or the editor(s) disclaim responsibility for any injury to people or property resulting from any ideas, methods, instructions or products referred to in the content.

Share and Cite

MDPI and ACS Style

Zhang, T.; Sun, J.; Peng, J.; Ding, Y.; Li, Y.; Ma, H.; Yu, M.; Ma, Y. Effects of Florfenicol on nirS-Type Denitrification Community Structure of Sediments in an Aquatic Microcosm Model. Antibiotics 2023, 12, 1254. https://doi.org/10.3390/antibiotics12081254

AMA Style

Zhang T, Sun J, Peng J, Ding Y, Li Y, Ma H, Yu M, Ma Y. Effects of Florfenicol on nirS-Type Denitrification Community Structure of Sediments in an Aquatic Microcosm Model. Antibiotics. 2023; 12(8):1254. https://doi.org/10.3390/antibiotics12081254

Chicago/Turabian Style

Zhang, Tengyue, Junying Sun, Jinju Peng, Yuexia Ding, Yang Li, Haotian Ma, Mengbo Yu, and Yi Ma. 2023. "Effects of Florfenicol on nirS-Type Denitrification Community Structure of Sediments in an Aquatic Microcosm Model" Antibiotics 12, no. 8: 1254. https://doi.org/10.3390/antibiotics12081254

APA Style

Zhang, T., Sun, J., Peng, J., Ding, Y., Li, Y., Ma, H., Yu, M., & Ma, Y. (2023). Effects of Florfenicol on nirS-Type Denitrification Community Structure of Sediments in an Aquatic Microcosm Model. Antibiotics, 12(8), 1254. https://doi.org/10.3390/antibiotics12081254

Note that from the first issue of 2016, this journal uses article numbers instead of page numbers. See further details here.

Article Metrics

Back to TopTop