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Article

Effect of Pond-Based Rice Floating Bed on the Microbial Community Structure and Quality of Water in Pond of Mandarin Fish Fed Using Artificial Diet

by
Lijin Jiang
1,†,
Mengmeng Yi
1,†,
Zhiyong Jiang
2,
Yuli Wu
2,
Jianmeng Cao
1,
Zhigang Liu
1,
Zhang Wang
1,
Maixin Lu
1,
Xiaoli Ke
1 and
Miao Wang
1,*
1
Key Laboratory of Tropical & Subtropical Fishery Resource Application & Cultivation, Ministry of Agriculture and Rural Affairs, Guangdong Provincial Key Laboratory of Aquatic Animal Immunology and Sustainable Aquaculture, Pearl River Fisheries Research Institute, Chinese Academy of Fishery Science, Guangzhou 510380, China
2
Guangdong Agricultural Technology Extension Center, Guangzhou 510520, China
*
Author to whom correspondence should be addressed.
†
These authors contributed equally to this work.
Biology 2024, 13(7), 549; https://doi.org/10.3390/biology13070549
Submission received: 21 June 2024 / Revised: 11 July 2024 / Accepted: 15 July 2024 / Published: 21 July 2024
(This article belongs to the Special Issue The Relationship between Water Quality and Aquatic Organisms)
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Abstract

:

Simple Summary

Simple Summary: This study presents the initial findings on how rice cultivation impacts water quality and the microbial community structure in ponds where mandarin fish are being fed an artificial diet. The results indicated that rice cultivation plays a significant role in reducing nutrient salt levels in the water, thus regulating the overall aquatic environment. Furthermore, the cultivation of rice has been found to alter the composition of microbial communities in the water, leading to a decrease in diversity and affecting the abundance of bacteria involved in carbon, nitrogen, and phosphorus metabolism. The study identified Proteobacteria, Actinobacteria, Firmicutes, Bacteroidetes, and Deinococcus-Thermus as the dominant bacterial phyla in ponds where mandarin fish are being fed an artificial diet. Additionally, it was observed that Proteobacteria showed a particular preference for proliferation in the aquatic environment with rice cultivation on the water surface. These results provide a valuable foundation for the potential application of aquaculture practices involving mandarin fish fed an artificial diet and rice floating beds.

Abstract

The culture of mandarin fish using artificial feed has been gaining increasing attention in China. Ensuring good water quality in the ponds is crucial for successful aquaculture. Recently, the trial of pond-based rice floating beds (PRFBs) in aquaculture ponds has shown promising results. This research assessed the impact of PRFBs on the microbial community structure and overall quality of the aquaculture pond, thereby enhancing our understanding of its functions. The results revealed that the PRFB group exhibited lower levels of NH4+-N, NO2−-N, NO3−-N, TN, TP, and Alk in pond water compared to the control group. The microbial diversity indices in the PRFB group showed a declining trend, while these indices were increasing in the control group. At the phylum level, there was a considerable increase in Proteobacteria abundance in the PRFB group throughout the culture period, suggesting that PRFBs may promote the proliferation of Proteobacteria. In the PRFB group, there was a remarkable decrease in bacterial populations related to carbon, nitrogen, and phosphorus metabolism, including genera Rhodobacter, Rhizorhapis, Dinghuibacter, Candidatus Aquiluna, and Chryseomicrobium as well as the CL500_29_marine_group. Overall, the research findings will provide a basis for the application of aquaculture of mandarin fish fed an artificial diet and rice floating beds.

1. Introduction

The mandarin fish or Chinese perch, scientifically known as Siniperca chuatsi (Basilewsky, 1855) (Perciformes: Percichthyidae), is a carnivorous species. Traditionally, the cultivation of mandarin fish relied on the use of live bait fish. However, the inadequate supply of bait fish has significantly hindered the growth of the mandarin fish aquaculture industry. It is estimated that four acres of bait fish ponds are required for every acre of mandarin fish cultivation. The feeding ratio for mandarin fish is high, with approximately four to five pounds of bait fish needed to produce one pound of mandarin fish. Consequently, this has resulted in increased costs for farmers. Fortunately, recent advancements in artificial feed technology specifically designed for mandarin fish have shown promising improvements in addressing these challenges. By 2022, aquaculture of mandarin fish using artificial feed in China has reached a rate of approximately 5%, yielding an output of 20,000 tons, according to the China Society of Fisheries [1]. Research has indicated that the nutritional composition of mandarin fish reared with artificial feed, particularly protein and amino acid content, was comparable to those fed bait fish diet. Additionally, these fish demonstrated a superior fatty acid profile with elevated levels of eicosapentaenoic acid (EPA) and docosahexaenoic acid (DHA) reported by Niu et al. (2023) [2]. However, it has been observed by Li et al. (2017) [3] that the diversity of intestinal microorganisms was lower in mandarin fish fed artificial feeds compared to those fed bait fish. Mandarin fish following an artificial diet displayed reduced gut microbial diversity and lower levels of certain enzymes, such as alkaline phosphatase (AKP), catalase (CAT), and lysozyme (LZM). Despite this progress, further research is urgently needed to optimize artificial feed-based aquaculture methods for mandarin fish.
The culture of mandarin fish demands high water quality standards. A study conducted by Gao et al. (2000) [4] indicated that mandarin fish ponds should maintain a suspended solids concentration of no more than 25 mg/L, a pH level between 6.5 and 8.5, and a dissolved oxygen level exceed 5 mg/L. Mandarin fish exhibited a high sensitivity to un-ionized ammonia, requiring concentrations below 0.025 mg/L. Hydrogen sulfide, NH4+-N, and NO2−-N levels should not exceed 0.1 mg/L, 1.0 mg/L, and 0.1 mg/L, respectively [5]. Thus, improvements in the water environmental conditions of mandarin fish aquaculture ponds are vital for the sustainable development of the industry.
Extensive studies have reported on the application of plant floating beds on environmental restoration. They showed that the floating bed cultivation of aquatic plants could reduce the levels of N, P, and other contaminants in water bodies [6] and was effective in treating pond water [7], eutrophic water [8], industrial wastewater [9], agricultural wastewater [10], and domestic sewage [11]. In this study, we utilized the pond-based rice floating beds (PRFBs) system for the cultivation of mandarin fish using artificial feed. This method differs from the traditional integrated rice-fish farming (IRFF) technique, which involves raising fish in rice paddy fields. IRFF has been successful in the production of various fish species, including Nile tilapia (Oreochromis niloticus) (Linnaeus, 1758) [12], African catfish (Clarias gariepinus) (Burchell, 1822) [13], yellow catfish (Pelteobagrus fulvidraco) (Richardson, 1846) [14], common carp (Cyprinus carpio) (Linnaeus, 1758) [12], mrigal carp (Cirrhinus mrigala) (Hamilton, 1822) [15], Asian seabass (Lates calcarifer) (Bloch, 1790) [16], major South Asian carp (Catla catla) (Hamilton, 1822) [15], rohu (Labeo rohita) (Hamilton, 1822) [15], and Dojo loach (Misgurnus anguillicaudatus) (Cantor, 1842) [17]. Several studies have examined the effects of PRFBs on the quality of pond water. For example, Goda et al. (2023) [18] discovered that PRFBs significantly enhanced the utilization of nitrogen (N) and phosphorus (P) in the water, while Zhu et al. (2023) [19] emphasized that this method effectively decreased the levels of N and P in water bodies. Although these studies suggested the potential of PRFBs to improve water quality, there has been a lack of comprehensive research on its impact on water quality and the associated microbial communities. Therefore, the objective of this study was to investigate the effects of PRFBs on water quality and the structure of microbial communities in mandarin fish ponds. This research provides insights for the utilization of PRFBs in aquaculture practices aimed at cultivating mandarin fish using an artificial diet.

2. Materials and Methods

2.1. Experimental Design

The aquaculture experiment was carried out at a farm located in Panyu, Guangzhou, Guangdong Province, China (Figure 1). Mandarin fish with an average body weight of 12.20 ± 8.43 g were fed an artificial feed in six ponds. Each pond was designated with a label: control-A, control-B, control-C, PRFB-A, PRFB-B, and PRFB-C. Notably, PRFB-A, PRFB-B, and PRFB-C had a rice cultivation area that accounted for 30% of the total pond area, with rice variety Meixiangzhan No. 2 being grown on high-density polyethylene floating beds (Table 1). All ponds sourced their aquaculture water from a reservoir. On 30 July 2022, measurements were taken to assess water quality, including total phosphorus (TP), alkalinity (Alk), total nitrogen (TN), nitrite–nitrogen (NO2−-N), nitrate–nitrogen (NO3--N), and total ammonia nitrogen (NH4+-N), and water from the reservoir was introduced into the experimental ponds (Table 2). Concurrently, rice cultivation was initiated on the floating beds within the PRFB group ponds.
Fish were fed twice a day at 2% to 4% of body mass using a commercial diet purchased from Foshan Nanhai Jieda Feed Co., Ltd. (Foshan, China). (Supplemental Table S1). The feeding amount was adjusted accordingly as the growth decreased, taking into consideration factors such as weather, water quality, and the feeding status of the fish. During the experiment, the water temperature ranged from 30 to 33 °C, pH was 7.5–8.2, the dissolved oxygen (DO) concentration was 7.56–8.70 mg/L, and total suspended solids (TSS) were 29.60–38.32 mg/L.

2.2. Sampling

We conducted a total of nine samplings, which were divided into three sampling periods. The first, second, and third samplings took place every three days from 20 August to 26 August (period I), 20 September to 26 September (period II), and 20 October to 26 October 2022 (period III), respectively. There were 54 water samples in total. We collected equal volumes of water from 30 cm below the surface at the four corners of each pond. The collected water was thoroughly mixed and then stored in sterile 250 mL water sampling bags. These water samples were later analyzed for their quality and filtered for sequencing. We utilized a 0.22 µm filter membrane with a filtration volume of 200 mL. The filter membranes were preserved at −80 ºC in freezers for subsequent high-throughput sequencing using the Illumina platform.

2.3. Method for Water Quality Measurement

We utilized methyl red as an indicator and conducted a titration on a 100 mL water sample using a known concentration of diluted hydrochloric acid to determine the alkalinity of the water. The concentrations of NH4+-N, NO2−-N, NO3−-N, and TP were measured using a multi-parameter water quality analyzer 5B-3B (Beijing Lianhua YongXing Science and Technology Development Co., Ltd., Beijing, China). The total nitrogen (TN) content was quantified using a total nitrogen analyzer LH-3B (Beijing Lianhua YongXing Science and Technology Development Co., Ltd., Beijing, China) (Table 3).

2.4. Illumina High-Throughput Sequencing

DNA from samples was isolated using the Quick-DNA™ Universal Kits (Zymo Research, Irvine, CA, USA). The V4 region of the 16S rRNA gene was amplified using the polymerase chain reaction (PCR) with the 515f/806r primer set: 5′-GTGCCAGCMGCCGCGGTAA-3′ and 5′-GGACTACHVGGGTWTCTAAT-3′. The library was constructed using the TruSeq® DNA PCR-Free Sample Preparation Kit (Illumina, Inc., San Diego, CA, USA) and quantified using Qubit and Q-PCR. Sequencing was performed on a NovaSeq 6000 (Illumina, San Diego, CA, USA) platform.

2.5. Data Processing and Statistical Analysis

High-throughput sequencing data were subjected to quality control (QC) using the Illumina standard workflow to ensure the integrity of the raw data. The filtered reads were then assembled into tags. Subsequently, the tags underwent further filtration, resulting in a set of clean tags for subsequent analysis.
The Usearch software (version 10.0) was utilized to cluster tags, operating at a 97% similarity threshold, to generate operational taxonomic units (OTUs). The taxonomic labels were assigned to these OTUs by annotating them using the Silva (Release132) taxonomic database (http://www.arb-silva.de, accessed 13 February 2023). Subsequently, the representative sequences for each OTU were aligned against microbial reference databases to obtain species classification information. The community composition of each sample was then analyzed at various taxonomic levels. To generate species abundance tables at different taxonomic ranks and calculate α diversity indices, the QIIME2 software (version 2019.4) was utilized. Based on the species abundance matrix and the classification data, the partial least squares discriminant analysis (PLS-DA) model was created by R to study the structural variation in microbial communities. LEfSe (linear discriminant analysis effect size) was performed to detect differentially abundant taxa across groups using the default parameters. Spearman’s rank correlation was performed to identify correlations between the water quality and relative abundances of genera among water microbiota. The “pheatmap” package in R was used to generate heat maps, and the “correlation” clustering method was used for the “pheatmap” function. Co-occurrence networks were inferred based on a Spearman correlation matrix and constructed using only significant correlation. The cutoff for correlation coefficients was determined to be 0.6, and the cutoff for p-values was 0.05. To further explore the impact of microbial community change, functional prediction with FAPROTAX annotation tool (https://pages.uoregon.edu/slouca/LoucaLab/archive/FAPROTAX/lib/php/index.php, accessed 10 July 2024) was performed. The predicted results were visualized by an LEfSe by R.
The experimental results were expressed as mean values ± standard error.

3. Results

3.1. Analysis of Water Quality Parameters

The results indicated that the alkalinity (Alk) concentration in the aquaculture water of the control group exhibited an initial decline followed by an increase, whereas it consistently increased in the PRFB group. Conversely, the NH4+-N concentration in the control group experienced an initial rise followed by a decrease, while it demonstrated negligible changes in the PRFB group. The concentrations of NO2−-N and NO3−-N in both the control and PRFB groups exhibited a similar pattern with an initial increase followed by a decrease. Nevertheless, overall, the PRFB group displayed lower levels of NO2−-N, NO3−-N, TN, and TP in comparison to the control group (Figure 2). Water quality measurements taken in individual ponds during different sampling periods are presented in the Supplemental Table S2. The results indicated that there were no significant differences between the control ponds within the same period. For the PRFB ponds, there were significant differences in ALK and NO2−-N levels during period III, with all others showing no significant differences within the same period. To further explore these findings, the levels of TN and TP in water samples from the two groups during period III were compared. It was revealed that the TN and TP levels in the PRFB ponds decreased by approximately 30.62% and 19.63%, respectively, in comparison to the control group by the end of the experiment.

3.2. Analysis of Illumina High-Throughput Sequencing Results

3.2.1. α-Diversity Analysis

Pond control-C did not achieve successful aquaculture; hence, two control ponds were included in the analysis of Illumina high-throughput sequencing. There were six replicates for the control group and nine replicates for the PRFB group in each sampling period in total. Rarefaction curve analysis showed that the curves eventually reached a considerably flat plateau, demonstrating that the sample sizes of sequencing were sufficient and covered the full diversity of the samples (Figure 3).
The results demonstrated that in period III, the Chao1 index of the control group increased, while that of the PRFB group decreased. The Simpson index remained relatively stable in the control group during period I and II but increased in period III. The Simpson index in the PRFB group increased in period II and decreased in period III. Overall, the richness and diversity of bacterial communities of the control group were found to be higher than that of the PRFB group (Figure 4).

3.2.2. β-Diversity Analysis

The microbial composition differences among the samples were analyzed using the PLSDA analysis method. The results of the PLSDA analysis for the control group and the PRFB group showed that PCA 1 accounted for 11.38% of the variations observed in the samples, while PCA 2 accounted for 4.62% of the variations. Significant differences in the structure of the microbial communities were observed between the control group and the PRFB group (Figure 5).

3.3. Spearman Correlation Analysis between Water Quality Parameters and Microbial Communities at the Genus Level

The Spearman correlation analysis was conducted to investigate the relationship between the abundance of the top 30 bacterial genera in the aquaculture ponds and selected water quality parameters. The results revealed a significant positive correlation between NO3−-N and Mycobacterium (p < 0.05). Moreover, Alk showed a significant negative correlation with Thermomonas (p < 0.05), Leucobacter (p < 0.01), and Comamonas (p < 0.05). TN exhibited a significant positive correlation with Aeromonas (p < 0.01) and Lactococcus (p < 0.05), while it showed a significant negative correlation with Leucobacter (p < 0.01) and Novosphingobium (p < 0.05). TP demonstrated a significant negative correlation with Leucobacter (p < 0.05). Additionally, NH4+-N exhibited a significant negative correlation with Brevundimonas (p < 0.05). NO2−-N was significantly negatively correlated with Comamonas (p < 0.01) (Figure 6).

3.4. Analysis of Microbial Community Composition

The results revealed that the predominant phyla present in the pond water of both the control group and the PRFB group were similar. Proteobacteria, Actinobacteria, Firmicutes, Bacteroidetes, and Deinococcus-Thermus exhibited high relative abundances in both the control and PRFB groups. Additionally, it was observed that as the aquaculture experiment progressed, the abundance of Proteobacteria increased in both the control and PRFB groups (Figure 7).
On the genus level, it was observed that during the aquaculture experiment, Acinetobacter was a dominant genus and remained stable in both the control and PRFB groups with no significant changes in abundance during periods I, II, and III. Exiguobacterium showed a noticeable decrease in abundance as the experiment progressed in both the control and PRFB groups. The abundance of Deinococcus showed a pattern of decrease followed by an increase in both the control and PRFB groups. The abundance of Mycobacterium exhibited an increasing trend in both the control and PRFB groups. In the control group, the abundance of Chryseobacterium initially increased and then decreased. In the PRFB group, the abundance of Chryseobacterium continued to increase. The abundance of Cloacibacterium increased and then decreased in the control group, while it continuously decreased in the PRFB group. In the control group, the abundance of Pseudomonas initially decreased and then increased. However, in the PRFB group, the abundance of Pseudomonas initially increased and then decreased. In the control group, the abundance of Enterobacter showed a decreasing trend, while in the PRFB group, it showed an increasing trend (Figure 8).

3.5. Analysis of Differential Bacterial Genera

LEfSe applied linear discriminant analysis to identify taxa with significant differences in abundance. The results showed that there were significant differences in the relative abundance of 3 phyla and 13 genera between the control III and PRFB III samples (p < 0.05). Among them, the relative abundances of Chloroflexi and Verrucomicrobia in the control III sample were significantly higher than those in the PRFB III sample, and the relative abundance of Proteobacteria was significantly lower than that in the PRFB III sample (p < 0.05). In addition, the relative abundances of Rhodobacter, KD4-96 (Chloroflexi), 67-14 (Actinobacteria), Rhizorhapis, Dinghuibacter, Candidatus_Aquiluna (Actinobacteria), LD29 (Verrucomicrobia), Chryseomicrobium, JG30_KF_CM45 (Chloroflexi), CL500-29_marine_group (Actinobacteria), and Elizabethkingia were significantly higher in the control III sample compared to the PRFB III sample. On the other hand, Kocuria and Chitinophaga showed significantly higher relative abundances in the PRFB III sample (p < 0.05) (Figure 9).

3.6. The Correlation Network Analysis

Control samples had more nodes (181) and edges (506) as well as higher connectance (0.0257) compared to the PRFB samples (nodes  = 124, edges  =  277, and connectance  =  0.0136) (Figure 10). These results indicated that microorganisms from control groups are more interrelated than those from PRFB groups.

3.7. Function Analysis

For FAPROTAX analysis, chemoheterotrophy, aerobic chemoheterotrophy, aromatic compound degradation, fermentation, and nitrate reduction were found among the top 5 most abundant functions (Figure 11A). The results of FAPROTAX showed significant changes in the abundance of some metabolic pathways of microbiota community of the water samples (Figure 11B). Most of these pathways involved nitrogen and sulfur metabolism, including sulfate respiration, the respiration of sulfur compounds, nitrate reduction, and nitrogen fixation. Those genes increased in the PRFB group compared to the control group.

4. Discussion

The stability of the pond’s ecological environment is crucial for the optimal growth of fish. The physicochemical properties and microbial community structure of the aquaculture water play a vital role in ensuring the success of the aquaculture process. It is of importance to implement new culture systems to improve water resource management practices [20]. These innovative methods effectively enhance water use efficiency and nitrogen and phosphorus use efficiency, and they also facilitate adjustments to the microbial community structure [21].
The PRFB is a new integrated aquaculture system. Our study revealed that the PRFB aquaculture system demonstrated lower concentrations of Alk, NH4+-N, NO2−-N, NO3−-N, TN, and TP compared to the control group. These findings suggest that rice cultivation in the PRFB system effectively absorbs nutrients from the water, and it enhances environmental nutrient utilization efficiency. These conclusions are in line with previous studies on IRFF and floating beds of aquatic plants [7,9,22,23,24]. Rice is capable of absorbing and utilizing NH4+-N and NO3−-N through its root system [25,26]. However, there is still limited research on the interaction mechanism between Alk and rice in water. Some studies have suggested that rice roots secrete organic acids [27]. Furthermore, the conversion of NH4+-N and NO2−-N in water is dependent on the consumption of Alk, including processes such as nitrification, denitrification, and algal photosynthesis [28,29]. Therefore, it can be inferred that the decrease in Alk following rice planting may be attributed to the above mechanism.
Using Spearman correlation analysis, we identified eight bacterial genera that are significantly correlated with water quality indicators and may contribute to nitrogen and phosphorus cycling. These genera included Mycobacterium, Thermomonas, Leucobacter, Comamonas, Aeromonas, Lactococcus, Novosphingobium, and Brevundimonas. Previous research has shown that certain species of Mycobacterium, such as M. vaccae and M. smegmatis, contained genes encoding for nitrate reductase, allowing them to convert NO3−-N to NO2−-N [30]. Aeromonas and Lactococcus carried genes that enable the stable removal of NH4+-N and TN [31]. Novosphingobium was an important denitrifying bacterium that was significantly positively correlated with N2O emissions [32]. Brevundimonas was effective in converting NH4+-N to NO2−-N [33]. A study conducted by Zhu et al. (2023) [34] on wastewater treatment found a negative correlation between Leucobacter and TP, which was consistent with the findings of our current study. Alk refers to the combined amount of acidic and alkaline substances in water, which is used to indicate the acidity or alkalinity of the water. In a sulfur-oxidizing denitrification filter, Thermomonas had a lower relative abundance in the Alk-raised group compared to the unadjusted group [35]. Furthermore, Comamonas efficiently removed NO2−-N from water [36], and Zheng et al. (2014) [37] discovered that when using Comamonas for the treatment of highly alkaline wastewater from a paper mill (pH 13.2~13.5), this bacterium did not require additional carbon sources for water treatment. During the treatment process, it can produce various acidic compounds, which may lead to a decrease in the alkalinity of the water.
This study presented the first application of PRFBs in mandarin fish farming. The β-diversity analysis of the microbial community revealed significant differences between the PRFB group and the control group in terms of microbial community structure. Interestingly, the study found that the PRFB group had lower α-diversity, as indicated by the Chao1, Simpson, and Shannon indices, compared to the control group. This suggested that growing rice on the pond surface in the PRFB group leads to a reduction in microbial diversity in the water. Previous studies have also reported a decrease in soil microbial diversity with IRFF [38,39,40]. Similarly, in an IRFF system in Sleman, Yogyakarta, Indonesia, it was observed that microbial diversity in the culture water decreased after rice cultivation [39]. This can be attributed to the direct absorption and utilization of nutrients by rice plants when grown on the pond surface, which could limit the growth of certain microorganisms.
The dominant bacterial phyla in both the PRFB group and control group at the end of the experiment (Period III) were Proteobacteria, Actinobacteria, Firmicutes, Bacteroidetes, and Deinococcus-Thermus, which were commonly found in water environments and sediment [41]. However, the LEfSe analysis revealed significant differences between the PRFB group and the control group in terms of the phyla Proteobacteria. Specifically, the relative abundance of Proteobacteria increased significantly in the water of the PRFB group, which was consistent with previous studies on IRFF [38,42]. Proteobacteria are known for their role in organic matter decomposition, producing various types of glycoside hydrolases and participating in nitrogen fixation to promote plant growth [43].
We have identified 13 genera that displayed significant differences in abundance based on LEfSe differential analysis. Our study revealed that the abundance of Kocuria and Chitinophaga in the PRFBs water was significantly higher compared to the control. Conversely, the abundance of Rhodobacter, KD4-96, 67-14, Rhizorhapis, Dinghuibacter, Candidatus_Aquiluna, LD29, Chryseomicrobium, JG30_KF_CM45, CL500_29_marine_group, and Elizabethkingia in the PRFBs water was significantly lower compared to the control water. Chitinophaga bacteria were capable of degrading chitin and converting nitrate into nitrite and nitrogen gas [44]. Rhodobacter bacteria belonged to the group of purple nonsulfur bacteria, many of which were capable of photosynthesis under sunlight. They typically used organic compounds as electron donors and simultaneously reduced the organic content of water during photosynthesis [45,46,47]. Rhizorhapis was capable of converting nitrogen gas into ammonia [48,49,50]. Dinghuibacter was commonly found in freshwater lakes, rivers, ponds, and other water bodies [51]. Its main sources of carbon were oligosaccharides and glucose, while ammonia and nitrate served as its nitrogen sources. Some strains of Dinghuibacter can also degrade toxic substances, making them potentially valuable in environmental remediation [52]. The 67–14, Candidatus_Aquiluna, and CL500-29_marine_groups were classified under the phylum Actinobacteria. 67–14 was an efficient degrader of various organic and inorganic carbon compounds, and it showed a significant positive correlation with phosphorus [53,54]. This suggested that 67–14 was capable of removing both organic and inorganic carbon compounds as well as phosphorus from water. Li et al. (2020) [55] discovered a positive correlation between Candidatus_Aquiluna and ammonia levels. The CL500-29_marine_group (Actinobacteria) was a dominant bacterial genus found in both water samples and sediments. It played a crucial role in carbon metabolism in aquatic environments by utilizing dissolved organic carbon under aerobic conditions [41,56]. Additionally, the unclassified genus KD4-96, belonging to Chloroflexi, demonstrated diverse metabolic activities and ecological functions. It was capable of biodegrading halosulfuron methyl and oxidizing nitrite [57,58]. JG30_KF_CM45 (Chloroflexi) was positively correlated with nitrate and total nitrogen [59,60,61]. LD29 (Verrucomicrobia) has been found to have a wide distribution and strong correlation with other bacterial species in a tropical estuarine reservoir, as highlighted by Xu et al. (2018) [62] and Zwart et al. (1998) [63]. In a study conducted by Mohapatra et al. (2019) [64], it was identified that LD29 primarily obtained its carbon source from Synechococcus in aquatic environments. The researchers speculated that LD29 may play a crucial role in the carbon cycle by decomposing organic compounds derived from phytoplankton. Chryseomicrobium bacteria were well known for their distinct physiological characteristics, including high tolerance to temperature and salinity, which allowed them to thrive in diverse environments [65]. Additionally, Wu et al. [66] discovered that Chryseomicrobium bacteria had the ability to degrade organic substances and exhibit denitrification functions. In the present research, reductions in the abundance of bacterial genera associated with water treatment were observed after rice cultivation in water. This difference in abundance may be due to the optimization of water conditions resulting from the presence of rice, which reduced the growth of those water treatment bacteria.
The functional analysis of the microbial community revealed that the water samples in the PRFB group showed an increased abundance of metabolic pathways related to nitrogen metabolism. Previous studies have shown that microbial nitrogen fixation is a crucial natural source of reactive nitrogen in floating treatment wetlands [67]. Additionally, in a combined treatment system comprising hydroponic plants and biofilm, nitrate reduction was identified as one of the main functions of the microbiota [68]. Therefore, it can be inferred that PRFBs enhance the microbiota’s function in water, specifically in nitrate reduction and nitrogen fixation, leading to an improvement in nitrogen metabolism in pond water, which was consistent with those previous results.

5. Conclusions

This study is the first report on the impact of rice cultivation on both water quality and the microbial community structure in ponds of mandarin fish fed an artificial diet. The results revealed that rice cultivation reduces nutrient salt levels in the water, regulating the aquatic environment. Simultaneously, rice cultivation modified the microbial community in the water by decreasing diversity and affecting its composition, particularly affecting bacteria that are involved in carbon, nitrogen, and phosphorus metabolism such as KD4-96, Rhizorhapis, Dinghuibacter, Candidatus_Aquiluna, Chryseomicrobium, and JG30_KF_CM45, resulting in their decreased abundance. Additionally, this study identified Proteobacteria, Actinobacteria, Firmicutes, Bacteroidetes, and Deinococcus-Thermus as the dominant bacterial phyla in ponds of mandarin fish fed an artificial diet. Furthermore, this research observed a distinct preference for the proliferation of Proteobacteria in the aquatic environment with rice cultivation on the water surface. These findings provided a theoretical foundation for the application of aquaculture of mandarin fish fed an artificial diet and rice floating beds.

Supplementary Materials

The following supporting information can be downloaded at https://www.mdpi.com/article/10.3390/biology13070549/s1, Table S1: Ingredients and chemical compositions of artificial feed; Table S2: Water quality in individual pond of different sampling periods.

Author Contributions

Conceptualization, L.J., X.K. and M.W.; methodology, L.J. and M.Y.; software, L.J. and Z.W.; formal analysis, J.C.; investigation, L.J. and Z.L.; resources, Z.J. and Y.W.; data curation, M.Y.; writing—original draft preparation, L.J.; writing—review and editing, M.W.; visualization, L.J.; supervision, X.K. and M.L.; project administration, M.W.; funding acquisition, M.W. and X.K. All authors have read and agreed to the published version of the manuscript.

Funding

This research was funded by the following grants: China Agriculture Research System of MOF and MARA (CARS-46), National Natural Science Foundation of China (32102818), Guangdong Basic and Applied Basic Research Foundation (2023A1515012379), Guangzhou Science and Technology Plan Project (2023E04J0002, 2024B03J1264), China, 2022 construction of aquaculture seed industry system—Integrative scientific research and enterprise consortium for tilapia breeding, reproduction and pushing (YueCaiNong 2022 No.119).

Institutional Review Board Statement

Not applicable.

Informed Consent Statement

Not applicable.

Data Availability Statement

The sequencing data have been uploaded to the NCBI Sequence Read Archive repository at https://www.ncbi.nlm.nih.gov (accessed on 1 February 2023), reference number PRJNA1071861.

Conflicts of Interest

The authors declare no conflicts of interest. The funders had no role in the design of the study; in the collection, analyses, or interpretation of data; in the writing of the manuscript; or in the decision to publish the results.

References

  1. China Society of Fisheries. China Fishery Statistical Yearbook; China Agriculture Press: Beijing, China, 2023. (In Chinese) [Google Scholar]
  2. Niu, S.H.; Li, H.Y.; Pan, H.J.; Xie, J.; Wang, G.J.; Xia, Y.; Gong, W.B. Effects of live prey fish and artificial diet on nutrient compositions and texture properties in the muscle of mandarin fish (Siniperca chuatsi). Acta Hydrob. Sin. 2023, 47, 37–44. (In Chinese) [Google Scholar] [CrossRef]
  3. Li, Y.; Li, J.; Lu, J.; Li, Z.; Shi, S.; Liu, Z. Effects of live and artificial feeds on the growth, digestion, immunity and intestinal microflora of mandarin fish hybrid (Siniperca chuatsi♀ × Siniperca scherzeri♂). Aquac. Res. 2017, 48, 4479–4485. [Google Scholar] [CrossRef]
  4. Gao, Y.A.; Xia, X.P.; Zhu, S.H. Appropriate water quality and management measures for main cultivation of mandarin fish ponds. Cur. Fish. 2000, 25, 29–30. (In Chinese) [Google Scholar]
  5. Cao, X.; Li, J.J. Ecological and high-profit intensive culture technique for mandarin fish in pond. Sci. Fish Farm. 2021, 05, 44–46. (In Chinese) [Google Scholar] [CrossRef]
  6. Huang, L.; Zhuo, J.; Guo, W.; Spencer, R.G.; Zhang, Z.; Xu, J. Tracing organic matter removal in polluted coastal waters via floating bed phytoremediation. Mar. Pollut. Bull. 2013, 71, 74–82. [Google Scholar] [CrossRef]
  7. Li, W.; Li, Z. In situ nutrient removal from aquaculture wastewater by aquatic vegetable Ipomoea aquatica on floating beds. Water Sci. Technol. 2009, 59, 1937–1943. [Google Scholar] [CrossRef]
  8. Cao, W.; Zhang, Y. Removal of nitrogen (N) from hypereutrophic waters by ecological floating beds (EFBs) with various substrates. Ecol. Eng. 2014, 62, 148–152. [Google Scholar] [CrossRef]
  9. Younas, A.; Kumar, L.; Deitch, M.J.; Qureshi, S.S.; Shafiq, J.; Ali Naqvi, S.; Kumar, A.; Amjad, A.Q.; Nizamuddin, S. Treatment of industrial wastewater in a floating treatment wetland: A case study of Sialkot Tannery. Sustainability 2022, 14, 12854. [Google Scholar] [CrossRef]
  10. Huett, D.; Morris, S.; Smith, G.; Hunt, N. Nitrogen and phosphorus removal from plant nursery runoff in vegetated and unvegetated subsurface flow wetlands. Water Res. 2005, 39, 3259–3272. [Google Scholar] [CrossRef]
  11. Abed, S.N.; Almuktar, S.A.; Scholz, M. Remediation of synthetic greywater in mesocosm—Scale floating treatment wetlands. Ecol. Eng. 2017, 102, 303–319. [Google Scholar] [CrossRef]
  12. Frei, M.; Becker, K. A greenhouse experiment on growth and yield effects in integrated rice–fish culture. Aquaculture 2005, 244, 119–128. [Google Scholar] [CrossRef]
  13. Bello, U.; Girei, I.; Maradun, H.; Bukar, A. Comparative study of two varieties of rice (FARO 44 and FARO 60) on growth performance of African catfish (Clarias gariepinus) in fish cum rice integrated system. Int. J. Fish. Aquat. Stud. 2020, 8, 261–264. [Google Scholar]
  14. Li, F.; Sun, Z.; Qi, H.; Zhou, X.; Xu, C.; Wu, D.; Fang, F.; Feng, J.; Zhang, N. Effects of rice-fish co-culture on oxygen consumption in intensive aquaculture pond. Rice Sci. 2019, 26, 50–59. [Google Scholar] [CrossRef]
  15. Mohanty, R.K.; Verma, H.; Brahmanand, P. Performance evaluation of rice–fish integration system in rainfed medium land ecosystem. Aquaculture 2004, 230, 125–135. [Google Scholar] [CrossRef]
  16. Tarigan, N.B.; Goddek, S.; Keesman, K.J. Explorative study of aquaponics systems in Indonesia. Sustainability 2021, 13, 12685. [Google Scholar] [CrossRef]
  17. Hu, L.; Zhang, J.; Ren, W.; Guo, L.; Cheng, Y.; Li, J.; Li, K.; Zhu, Z.; Zhang, J.; Luo, S.; et al. Can the co-cultivation of rice and fish help sustain rice production? Sci. Rep. 2016, 6, 28728. [Google Scholar] [CrossRef]
  18. Goda, A.M.S.; Aboseif, A.M.; Mohammedy, E.Y.; Taha, M.K.; Mansour, A.I.; Ramadan, E.A.; Aboushabana, N.M.; Zaher, M.M.; Otazua, N.I.; Ashour, M. Earthen pond-based floating beds for rice-fish co-culture as a novel concept for climate adaptation, water efficiency improvement, nitrogen and phosphorus management. Aquaculture 2024, 579, 740215. [Google Scholar] [CrossRef]
  19. Zhu, J.; Wei, R.; Wang, X.; Jiang, X.; Wang, M.; Yang, Y.; Yang, L. The ppk-expressing transgenic rice floating bed improves P removal in slightly polluted water. Environ. Res. 2023, 231, 116261. [Google Scholar] [CrossRef]
  20. Ahmed, N.; Hornbuckle, J.; Turchini, G.M. Blue–green water utilization in rice–fish cultivation towards sustainable food production. Ambio 2022, 51, 1933–1948. [Google Scholar] [CrossRef]
  21. Somerville, C.; Cohen, M.; Pantanella, E.; Stankus, A.; Lovatelli, A. Small-Scale Aquaponic Food Production: Integrated Fish and Plant Farming; FAO Fisheries and Aquaculture Technical Paper 598; Food and Agriculture Organization of the United Nations: Rome, Italy, 2014. [Google Scholar]
  22. Wang, W.H.; Wang, Y.; Sun, L.Q.; Zheng, Y.C.; Zhao, J.C. Research and application status of ecological floating bed in eutrophic landscape water restoration. Sci. Total Environ. 2020, 704, 135434. [Google Scholar] [CrossRef]
  23. Feng, J.; Li, F.; Zhou, X.; Xu, C.; Fang, F. Nutrient removal ability and economical benefit of a rice-fish co-culture system in aquaculture pond. Ecol. Eng. 2016, 94, 315–319. [Google Scholar] [CrossRef]
  24. Li, F.; Feng, J.; Zhou, X.; Liu, Y.; Xu, C.; Ji, L.; Chen, Z.; Jijakli, M.H.; Fang, F.; Zhang, W. Effect of rice-fish/shrimp co-culture on sediment resuspension and associated nutrients release in intensive aquaculture ponds. Arch. Agron. Soil Sci. 2020, 66, 971–982. [Google Scholar] [CrossRef]
  25. Yoneyama, T.; Matsumaru, T.; Usui, K.; Engelaar, W. Discrimination of nitrogen isotopes during absorption of ammonium and nitrate at different nitrogen concentrations by rice (Oryza sativa L.) plants. Plant Cell Environ. 2001, 24, 133–139. [Google Scholar] [CrossRef]
  26. Hayashi, K.; Nishimura, S.; Yagi, K. Ammonia volatilization from a paddy field following applications of urea: Rice plants are both an absorber and an emitter for atmospheric ammonia. Sci. Total Environ. 2008, 390, 485–494. [Google Scholar] [CrossRef]
  27. Delhaize, E.; Ryan, P.R. Aluminum toxicity and tolerance in plants. Plant Physiol. 1995, 107, 315. [Google Scholar] [CrossRef]
  28. Ma, T.; Luo, G.Z.; Tan, H.X.; Chen, W. Effect of Alkalinity on nitrogen conversion and biological characteriztion of bioflcs process in aquaculture. Fish. Sci. 2017, 36, 421–428. (In Chinese) [Google Scholar] [CrossRef]
  29. Sun, Y.; Zeng, J.N.; Wu, Y.L. Study on the relationship between basicity and NH3-N in a wastewater treament system. Technol. Water Treat. 2022, 48, 114–117. (In Chinese) [Google Scholar] [CrossRef]
  30. Amon, J.; Titgemeyer, F.; Burkovski, A. A genomic view on nitrogen metabolism and nitrogen control in mycobacteria. Microb. Physiol. 2009, 17, 20–29. [Google Scholar] [CrossRef]
  31. Tan, X.; Yang, Y.L.; Liu, Y.W.; Li, X.; Zhu, W.B. Quantitative ecology associations between heterotrophic nitrification-aerobic denitrification, nitrogen-metabolism genes, and key bacteria in a tidal flow constructed wetland. Bioresour. Technol. 2021, 337, 125449. [Google Scholar] [CrossRef] [PubMed]
  32. Sagar, A.; Rai, S.; Ilyas, N.; Sayyed, R.; Al-Turki, A.I.; El Enshasy, H.A.; Simarmata, T. Halotolerant rhizobacteria for salinity-stress mitigation: Diversity, mechanisms and molecular approaches. Sustainability 2022, 14, 490. [Google Scholar] [CrossRef]
  33. Liu, Y.; Ma, B.; Liu, Z. Application of a partial nitrogen lab-scale sequencing batch reactor for the treatment of organic wastewater and its N2O production pathways, and the microbial mechanism. Sustainability 2022, 14, 1457. [Google Scholar] [CrossRef]
  34. Zhu, S.; Deng, J.; Jin, X.; Wu, H.; Wei, C.; Qiu, G.; Preis, S.; Wei, C. Diverse and distinct bacterial community involved in a full-scale A/O1/H/O2 combination of bioreactors with simultaneous decarbonation and denitrogenation of coking wastewater. Environ. Sci. Pollut. Res. 2023, 30, 2103–2117. [Google Scholar] [CrossRef] [PubMed]
  35. Pan, H.; Cui, M.H.; Zhang, C.; Liu, L.Y.; Li, J.; Jiang, Q.; Zhang, X.D.; Zheng, Z.Y.; Zhang, Y.; Liu, H. Alkalinity regulation in a sulfur autotrophic denitrifying filter substantially reduced total dissolved solids and sulfate in effluent. Bioresour. Technol. 2022, 348, 126751. [Google Scholar] [CrossRef] [PubMed]
  36. Su, J.; Yang, S.; Huang, T.; Li, M.; Liu, J.; Yao, Y. Enhancement of the denitrification in low C/N condition and its mechanism by a novel isolated Comamonas sp. YSF15. Environ. Pollut. 2020, 256, 113294. [Google Scholar] [CrossRef] [PubMed]
  37. Zheng, Y.; Chai, L.; Yang, Z.; Chen, Y.; Shi, Y.; Wang, Y. Environmentally safe treatment of black liquor with Comamonas sp. B-9 under high-alkaline conditions. J. Basic Microbiol. 2014, 54, 152–161. [Google Scholar] [CrossRef] [PubMed]
  38. Arunrat, N.; Sansupa, C.; Kongsurakan, P.; Sereenonchai, S.; Hatano, R. Soil microbial diversity and community composition in rice–fish co-culture and rice monoculture farming system. Biology 2022, 11, 1242. [Google Scholar] [CrossRef] [PubMed]
  39. Herlambang, A.; Murwantoko, M.; Istiqomah, I. Dynamic change in bacterial communities in the integrated rice–fish farming system in Sleman, Yogyakarta, Indonesia. Aquac. Res. 2021, 52, 5566–5578. [Google Scholar] [CrossRef]
  40. Zhang, Y.; Chen, M.; Zhao, Y.Y.; Zhang, A.Y.; Peng, D.H.; Lu, F.; Dai, C.C. Destruction of the soil microbial ecological environment caused by the over-utilization of the rice-crayfish co-cropping pattern. Sci. Total Environ. 2021, 788, 147794. [Google Scholar] [CrossRef]
  41. Liu, Z.; Iqbal, M.; Zeng, Z.; Lian, Y.; Zheng, A.; Zhao, M.; Li, Z.; Wang, G.; Li, Z.; Xie, J. Comparative analysis of microbial community structure in the ponds with different aquaculture model and fish by high-throughput sequencing. Microb. Pathog. 2020, 142, 104101. [Google Scholar] [CrossRef]
  42. Zhang, C.; Mi, W.; Xu, Y.; Zhou, W.; Bi, Y. Long-term integrated rice-crayfish culture disrupts the microbial communities in paddy soil. Aquac. Rep. 2023, 29, 101515. [Google Scholar] [CrossRef]
  43. Aislabie, J.; Deslippe, J.R.; Dymond, J. Soil microbes and their contribution to soil services. In Ecosystem Services in New Zealand–Conditions and Trends; Manaaki Whenua Press: Lincoln, New Zealand, 2013; Volume 1, pp. 143–161. [Google Scholar]
  44. Kim, M.K.; Jung, H.Y. Chitinophaga terrae sp. nov., isolated from soil. Int. J. Syst. Evol. Microbiol. 2007, 57, 1721–1724. [Google Scholar] [CrossRef] [PubMed]
  45. Crofts, A.R. Photosynthesis in Rhodobacter sphaeroides. Trends Microbiol. 2000, 8, 105–106. [Google Scholar] [CrossRef] [PubMed]
  46. Imhoff, J.F. Rhodobacter. In Bergey’s Manual of Systematics of Archaea and Bacteria; John Wiley & Sons, Inc.: Hoboken, NJ, USA, 2015; pp. 1–12. [Google Scholar] [CrossRef]
  47. Koku, H.; Eroğlu, İ.; Gündüz, U.; Yücel, M.; Türker, L. Aspects of the metabolism of hydrogen production by Rhodobacter sphaeroides. Int. J. Hydrogen Energy 2002, 27, 1315–1329. [Google Scholar] [CrossRef]
  48. Ishiyama, Y.; Ogiso, H.; Furuta, G. Corky root of lettuce caused by Rhizorhapis suberifaciens in Japan. J. Gen. Plant Pathol. 2022, 88, 150–154. [Google Scholar] [CrossRef]
  49. Fischer, H.M. Genetic regulation of nitrogen fixation in rhizobia. Microbiol. Rev. 1994, 58, 352–386. [Google Scholar] [CrossRef]
  50. Zahran, H.H. Rhizobium-legume symbiosis and nitrogen fixation under severe conditions and in an arid climate. Microbiol. Mol. Biol. Rev. 1999, 63, 968–989. [Google Scholar] [CrossRef]
  51. Dai, L.; Liu, C.; Peng, L.; Song, C.; Li, X.; Tao, L.; Li, G. Different distribution patterns of microorganisms between aquaculture pond sediment and water. J. Microbiol. 2021, 59, 376–388. [Google Scholar] [CrossRef] [PubMed]
  52. Gao, Y.; Zhang, Y.; Wei, Q.; Qi, X.; Yin, Q.; Liu, B.; He, K. Response and synergistic effect of microbial community to submerged macrophyte in restoring urban black and smelly water bodies. J. Water Process. Eng. 2023, 53, 103906. [Google Scholar] [CrossRef]
  53. Lin, W.; Fan, F.; Xu, G.; Gong, K.; Cheng, X.; Yuan, X.; Zhang, C.; Gao, Y.; Wang, S.; Ng, H.Y.; et al. Microbial community assembly responses to polycyclic aromatic hydrocarbon contamination across water and sediment habitats in the Pearl river estuary. J. Hazard. Mater. 2023, 457, 131762. [Google Scholar] [CrossRef]
  54. Guo, J.; Dou, W.; Liu, Z.; Sun, J.; Xu, D.; Yang, Q.; Lv, G.; Wang, D. Long-term heavy metal pollution induces complex differences in farmland topsoil and rhizosphere microbial communities. Sustainability 2023, 15, 16598. [Google Scholar] [CrossRef]
  55. Li, N.; Chen, X.; Zhao, H.; Tang, J.; Jiang, G.; Li, Z.; Li, X.; Chen, S.I.; Zou, S.; Dong, K.; et al. Spatial distribution and functional profile of the bacterial community in response to eutrophication in the subtropical Beibu Gulf, China. Mar. Pollut. Bull. 2020, 161, 111742. [Google Scholar] [CrossRef]
  56. Gómez-Consarnau, L.; Lindh, M.V.; Gasol, J.M.; Pinhassi, J. Structuring of bacterioplankton communities by specific dissolved organic carbon compounds. Environ. Microbiol. 2012, 14, 2361–2378. [Google Scholar] [CrossRef] [PubMed]
  57. Wang, Y.; Du, L.; Liu, H.; Long, D.; Huang, M.; Wang, Y.; Huang, S.; Jin, D. Halosulfuron methyl did not have a significant effect on diversity and community of sugarcane rhizosphere microflora. J. Hazard. Mater. 2020, 399, 123040. [Google Scholar] [CrossRef] [PubMed]
  58. Sorokin, D.Y.; Lücker, S.; Vejmelkova, D.; Kostrikina, N.A.; Kleerebezem, R.; Rijpstra, W.I.C.; Damsté, J.S.S.; Le Paslier, D.; Muyzer, G.; Wagner, M.; et al. Nitrification expanded: Discovery, physiology and genomics of a nitrite-oxidizing bacterium from the phylum Chloroflexi. ISME J. 2012, 6, 2245–2256. [Google Scholar] [CrossRef] [PubMed]
  59. Shen, M.C.; Zhang, Y.Z.; Bo, G.D.; Yang, B.; Wang, P.; Ding, Z.Y.; Wang, Z.B.; Yang, J.M.; Zhang, P.; Yuan, X.L. Microbial responses to the reduction of chemical fertilizers in the rhizosphere soil of flue-cured tobacco. Front. Bioeng. Biotechnol. 2022, 9, 812316. [Google Scholar] [CrossRef] [PubMed]
  60. Zhang, B.; Li, Z.L.; Bai, C.H.; Liu, J.L.; Nan, J.; Cao, D.; Li, L.W. Characteristics of groundwater microbial communities’ structure under the impact of elevated nitrate concentrations in north China plain. Environ. Res. 2023, 218, 115003. [Google Scholar] [CrossRef]
  61. Liu, G.; Ma, P.; Cheng, Z.; Wang, Y.; Li, Y.; Wu, X. Effects of thaw slump on soil bacterial communities on the Qinghai-Tibet Plateau. Catena 2023, 232, 107342. [Google Scholar] [CrossRef]
  62. Xu, Z.; Te, S.H.; He, Y.; Gin, K.Y.H. The characteristics and dynamics of cyanobacteria–heterotrophic bacteria between two estuarine reservoirs–tropical versus sub-tropical regions. Front. Microbiol. 2018, 9, 2531. [Google Scholar] [CrossRef] [PubMed]
  63. Zwart, G.; Huismans, R.; van Agterveld, M.P.; Van de Peer, Y.; De Rijk, P.; Eenhoorn, H.; Muyzer, G.; van Hannen, E.J.; Gons, H.J.; Laanbroek, H.J. Divergent members of the bacterial division Verrucomicrobiales in a temperate freshwater lake. FEMS Microbiol. Ecol. 1998, 25, 159–169. [Google Scholar] [CrossRef]
  64. Mohapatra, M.; Behera, P.; Kim, J.Y.; Rastogi, G. Seasonal and spatial dynamics of bacterioplankton communities in a brackish water coastal lagoon. Sci. Total Environ. 2020, 705, 134729. [Google Scholar] [CrossRef]
  65. Pindi, P.K.; Ashwitha, K.; Rani, A.S. Chryseomicrobium palamuruense sp. nov., a haloalkalitolerant bacterium isolated from a sediment sample. Int. J. Syst. Evol. Microbiol. 2016, 66, 3731–3736. [Google Scholar] [CrossRef] [PubMed]
  66. Wu, H.; Zhang, Q.; Chen, X.; Zhu, Y.; Yuan, C.; Zhang, C. The influence mechanism of DO on the microbial community and carbon source metabolism in two solid carbon source systems. Environ. Res. 2022, 206, 112410. [Google Scholar] [CrossRef] [PubMed]
  67. Shahid, M.J.; AL-surhanee, A.A.; Kouadri, F.; Ali, S.; Nawaz, N.; Afzal, M.; Rizwan, M.; Ali, B.; Soliman, M.H. Role of microorganisms in the remediation of wastewater in floating treatment wetlands: A review. Sustainability 2020, 12, 5559. [Google Scholar] [CrossRef]
  68. Li, P.; Wang, C.; Liu, G.; Luo, X.; Rauan, A.; Zhang, C.; Li, T.; Yu, H.; Dong, S.; Gao, Q. A hydroponic plants and biofilm combined treatment system efficiently purified wastewater from cold flowing water aquaculture. Sci. Total Environ. 2022, 821, 153534. [Google Scholar] [CrossRef] [PubMed]
Biology 13 00549 g001
Figure 1. (A) The sampling location; (B) the control pond; (C) the PRFB pond. The black dot indicates the sampling location.
Figure 1. (A) The sampling location; (B) the control pond; (C) the PRFB pond. The black dot indicates the sampling location.
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Figure 2. Changes in water quality in different groups. Note: Control I, Control II, and Control III represent the sample numbers in the control group for periods I, II, and III respectively. PRFB I, PRFB II, and PRFB III represent the sample numbers in the PRFB group for periods I, II, and III, respectively.
Figure 2. Changes in water quality in different groups. Note: Control I, Control II, and Control III represent the sample numbers in the control group for periods I, II, and III respectively. PRFB I, PRFB II, and PRFB III represent the sample numbers in the PRFB group for periods I, II, and III, respectively.
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Figure 3. Rarefaction curve. Note: C represents the sample number in the control group. P represents the sample number in the PRFB group.
Figure 3. Rarefaction curve. Note: C represents the sample number in the control group. P represents the sample number in the PRFB group.
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Figure 4. α- Diversity index analysis. Note: Control I, Control II, and Control III represent the sample numbers in the control group for periods I, II, and III respectively. PRFB I, PRFB II, and PRFB III represent the sample numbers in the PRFB group for periods I, II, and III, respectively.
Figure 4. α- Diversity index analysis. Note: Control I, Control II, and Control III represent the sample numbers in the control group for periods I, II, and III respectively. PRFB I, PRFB II, and PRFB III represent the sample numbers in the PRFB group for periods I, II, and III, respectively.
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Figure 5. PLSDA analysis between different groups.
Figure 5. PLSDA analysis between different groups.
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Figure 6. Spearman correlation analysis between water quality parameters and microbial communities at the genus level. Note: * represents p < 0.05, ** represents p < 0.01, and the correlation coefficient R > 0.3.
Figure 6. Spearman correlation analysis between water quality parameters and microbial communities at the genus level. Note: * represents p < 0.05, ** represents p < 0.01, and the correlation coefficient R > 0.3.
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Figure 7. Relative abundance of microbiota at the phylum level. Note: Control I, Control II, and Control III represent the sample numbers in the control group for periods I, II, and III, respectively. PRFB I, PRFB II, and PRFB III represent the sample numbers in the PRFB group for periods I, II, and III, respectively.
Figure 7. Relative abundance of microbiota at the phylum level. Note: Control I, Control II, and Control III represent the sample numbers in the control group for periods I, II, and III, respectively. PRFB I, PRFB II, and PRFB III represent the sample numbers in the PRFB group for periods I, II, and III, respectively.
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Figure 8. Relative abundance of microbiota at the genus level. Note: Control I, Control II, and Control III represent the sample numbers in the control group for periods I, II, and III, respectively. PRFB I, PRFB II, and PRFB III represent the sample numbers in the PRFB group for periods I, II, and III, respectively.
Figure 8. Relative abundance of microbiota at the genus level. Note: Control I, Control II, and Control III represent the sample numbers in the control group for periods I, II, and III, respectively. PRFB I, PRFB II, and PRFB III represent the sample numbers in the PRFB group for periods I, II, and III, respectively.
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Figure 9. LefSe analysis of microbial communities. Note: Control III and PRFB III represent the sample numbers for the control group and PRFB group, respectively, during the third sampling period; LDA discriminant analysis score threshold is 3, p < 0.05.
Figure 9. LefSe analysis of microbial communities. Note: Control III and PRFB III represent the sample numbers for the control group and PRFB group, respectively, during the third sampling period; LDA discriminant analysis score threshold is 3, p < 0.05.
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Figure 10. Correlation network analysis of water microbiota based on genus level: (A) control group (nodes  =  181, edges  =  507) and (B) PRFB group (nodes  =  124, edge  =  277). Spearman’s R  >  0.6; p  <  0.05.
Figure 10. Correlation network analysis of water microbiota based on genus level: (A) control group (nodes  =  181, edges  =  507) and (B) PRFB group (nodes  =  124, edge  =  277). Spearman’s R  >  0.6; p  <  0.05.
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Figure 11. FAPROTAX analysis of the water microbiota. (A) The relative abundance of top 10 functions; (B) LefSe analysis of functional composition of the water microbiota based on FAPROTAX. * p < 0.05; ** p < 0.01.
Figure 11. FAPROTAX analysis of the water microbiota. (A) The relative abundance of top 10 functions; (B) LefSe analysis of functional composition of the water microbiota based on FAPROTAX. * p < 0.05; ** p < 0.01.
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Table 1. Pond information.
Table 1. Pond information.
GroupsPond NumberPond Area
(hm2)		Density
(Tail/hm2)		Rice Planting
Area
ControlControl-A0.23460,0000
Control-B0.33060,0000
Control-C0.31060,0000
PRFBPRFB-A0.24060,00030%
PRFB-B0.41560,00030%
PRFB-C0.33060,00030%
Table 2. Water quality parameters of the reservoir.
Table 2. Water quality parameters of the reservoir.
Water Quality Parameters AlkNH4+-NNO2−-NNO3−-NTNTP
Concentration (mg/L)107.990.3650.02250.0241.5080.425
Table 3. Water quality measurement methods.
Table 3. Water quality measurement methods.
Water Quality
Parameters		Test Method
AlkalinitypH indicator titration
NH4+-NNessler’s reagent colorimetric method
NO2−-NN-(1-naphthyl) ethylenediamine photometric method
NO3−-NPhenol sulfonic acid spectrophotometry
TNPotassium persulfate ultraviolet spectrophotometry
TPMalachite green phosphomolybdate heteropoly metalate spectrophotometry
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Jiang, L.; Yi, M.; Jiang, Z.; Wu, Y.; Cao, J.; Liu, Z.; Wang, Z.; Lu, M.; Ke, X.; Wang, M. Effect of Pond-Based Rice Floating Bed on the Microbial Community Structure and Quality of Water in Pond of Mandarin Fish Fed Using Artificial Diet. Biology 2024, 13, 549. https://doi.org/10.3390/biology13070549

AMA Style

Jiang L, Yi M, Jiang Z, Wu Y, Cao J, Liu Z, Wang Z, Lu M, Ke X, Wang M. Effect of Pond-Based Rice Floating Bed on the Microbial Community Structure and Quality of Water in Pond of Mandarin Fish Fed Using Artificial Diet. Biology. 2024; 13(7):549. https://doi.org/10.3390/biology13070549

Chicago/Turabian Style

Jiang, Lijin, Mengmeng Yi, Zhiyong Jiang, Yuli Wu, Jianmeng Cao, Zhigang Liu, Zhang Wang, Maixin Lu, Xiaoli Ke, and Miao Wang. 2024. "Effect of Pond-Based Rice Floating Bed on the Microbial Community Structure and Quality of Water in Pond of Mandarin Fish Fed Using Artificial Diet" Biology 13, no. 7: 549. https://doi.org/10.3390/biology13070549

APA Style

Jiang, L., Yi, M., Jiang, Z., Wu, Y., Cao, J., Liu, Z., Wang, Z., Lu, M., Ke, X., & Wang, M. (2024). Effect of Pond-Based Rice Floating Bed on the Microbial Community Structure and Quality of Water in Pond of Mandarin Fish Fed Using Artificial Diet. Biology, 13(7), 549. https://doi.org/10.3390/biology13070549

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