Isolation and Identiﬁcation of an Efﬁcient Aerobic Denitrifying Pseudomonas stutzeri Strain and Characterization of Its Nitrite Degradation

: Nitrogen pollution in water bodies is becoming increasingly serious, and how to remove nitrogen from water bodies economically and effectively has become a research hotspot. Especially in recent years, with the gradual expansion of aquaculture in China, the content of nitrite and other nitrogen-containing substances in water bodies has been increasing, which inhibits the growth of farm animals and is one of the causes of eutrophication in water bodies. In this study, a strain of bacteria was isolated from the sludge of an aquaculture ﬁshpond and identiﬁed as Pseudomonas stutzeri , which can efﬁciently degrade nitrite. After continuous domestication in nitrite mixed solution, the nitrite nitrogen reduction capacity of P. stutzeri was signiﬁcantly improved. Univariate experiments aiming to optimize the degradation conditions indicate that the optimal culture conditions for strain F2 are: medium with a carbon source of sodium succinate; C/N of 18; pH of 8; culture temperature of 28 ◦ C; and shaking speed of 210 rpm in the shaker. Under the optimal culture conditions, the NO 2 − -N concentration of the culture solution was 300 mg/L, and the nitrite removal rate reached 98.67%. Meanwhile, the results of the nitrogen balance test showed that the strain converted 6.1% of the initial nitrogen into cellular organic nitrogen and 62.3% into gaseous nitrogen.


Introduction
In the aquaculture process, there is often a large amount of aquatic animal excrement, residual bait, and dead biological residues deposited on the bottom of the pond, resulting in the deterioration of the pond aquaculture water quality, the concentration of nitrogen such as sub-nitrate nitrogen in the water column seriously exceeding the standard amount, and the proliferation of harmful microorganisms [1]. Animals in the ponds are subject to long-term stress, resulting in increasingly serious disease, which not only causes huge economic losses to aquaculture farmers, but also gives rise to a series of aquatic product quality and safety issues. To reduce the harm caused by nitrite nitrogen and other nitrogen pollution, people often use water changes, aeration, drugs, and other methods of treatment, but there are great limitations, as these methods have high costs, a short duration, and require the use of drugs to make the germs drug resistant, as well as other disadvantages. Therefore, the search for new models of healthy aquaculture and the development of environmentally friendly products with disease control and water quality improvement has become a hot spot for research in the field of aquaculture. Many scholars believe that the most thorough way to restore an imbalanced pond ecosystem is to use microbial remediation methods [2,3].
Biological denitrification technology is the most effective denitrification technology due to its simple operation, low cost, and low secondary pollution [4,5]. The traditional biological denitrification theory suggests that the nitrification process is performed by aerobic autotrophic nitrifying bacteria, the denitrification process is performed by anoxic heterotrophic denitrifying bacteria, and the nitrification and denitrification processes occur in two separate environments and cannot be carried out in the same system. Therefore, traditional biological denitrification is not suitable for water source reservoirs. In the 1980s, Robertson et al. [6] successfully isolated Thiosphera pantotropha (now known as Paracoccus sp.), a denitrifying bacterium under aerobic conditions, from a Dutch desulfurization and denitrification system. This finding shows that nitrification and denitrification can take place in the same environment, while the alkali produced during denitrification can balance the acid produced during nitrification, and no additional acid or alkali is needed to neutralize the system during operation, opening up a new area of research [7].
With the continuous progress of research, some aerobic denitrifying bacteria, mainly Alcaligenes [8], Paracoccus [9], Pseudomonas [10], and Bacillus [11], have been isolated by domestic and foreign researchers. Among them, the most prevalent aerobic denitrifying bacteria in the environment are Pseudomonaceae, Alcaligenes, Paracoccus, etc. [12]. On the whole, the current research on heterotrophic nitrification-aerobic denitrification bacteria at home and abroad is still in the laboratory stage, including resource mining, denitrification characteristic research, denitrification mechanism research, and denitrification effect evaluation of simulated wastewater under aseptic conditions, while the practical application research in cultured water bodies is even more scarce [13,14].
In this study, highly active aerobic denitrifying bacteria were isolated and screened from the natural environment, and then continuously domesticated in different concentrations of nitrite mixed salt cultures to further improve their denitrification performance. Their culture conditions were optimized to achieve the best denitrification performance. This provides a theoretical basis and experimental data for research applications in aquaculture and helps the development and commercialization of microecological preparations, which has important theoretical research significance and practical application value.

Strain Selection
By testing the growth curve and nitrogen reduction performance of 10 aerobic denitrifying bacteria strains, it was found that strain F2 had efficient nitrogen reduction performance. Its growth rate and denitrification efficiency were much higher than other strains, and the bacterial concentration (OD 600 value) could reach 1.02 ( Figure 1A). Under the condition of a nitrite nitrogen concentration of 300 mg/L, and a shake flask fermentation culture for 36 h, the nitrite denitrification rate could reach 72.6% ( Figure 1B). Therefore, strain F2 was retained, and its strain identification and culture degradation conditions were optimized.

Identification of Strain F2
In the preliminary screening experiments, strain F2 showed the highest efficiency in the removal of nitrite. Strain F2 was Gram-negative, non-motile, and had a short rod shape. The mature colonies of strain F2 were prominently aqua, rugose, round, humid, translucent, and irregularly bordered. A portion of the 16S rRNA sequence of strain F2 was obtained by polymerase chain reaction (PCR). A homology search using Blast showed that strain F2 was most closely related to Pseudomonas stutzeri P3 and P. stutzeri HD4−1. Therefore, strain F2 was identified as P. stutzeri F2. Based on the adjoint method and GenBank database, a phylogenetic tree was established ( Figure 2).

Identification of Strain F2
In the preliminary screening experiments, strain F2 showed the highest efficiency in the removal of nitrite. Strain F2 was Gram-negative, non-motile, and had a short rod shape. The mature colonies of strain F2 were prominently aqua, rugose, round, humid, translucent, and irregularly bordered. A portion of the 16S rRNA sequence of strain F2 was obtained by polymerase chain reaction (PCR). A homology search using Blast showed that strain F2 was most closely related to Pseudomonas stutzeri P3 and P. stutzeri HD4−1. Therefore, strain F2 was identified as P. stutzeri F2. Based on the adjoint method and Gen-Bank database, a phylogenetic tree was established ( Figure 2). The phylogenetic tree of the F2 strain was obtained from neighbor-joining of partial 16S rRNA sequences, and the closed columns indicate the roots of the tree.

Analysis of the Results of Targeted Domestication
The nitrite tolerance of strain F2 was domesticated by the concentration gradient increment method. Before domestication, strain F2 was able to grow to a maximum OD600 of only 1.12 in a denitrification medium with an initial NO2 − -N concentration of 300 mg/L ( Figure 3A), while at an initial nitrosomal nitrogen concentration of 500 mg/L, strain F2 barely grew. After a period of domestication, the growth of the strain improved significantly, and the corresponding maximum OD600 was 2.38, 1.91, and 1.41 at initial NO2 − -N concentrations of 300, 400, and 500 mg/L, respectively, indicating that the domesticated F2 strain has significantly increased tolerance to NO2 − -N and can be applied to the treatment of nitrite wastewater at high concentrations.

Identification of Strain F2
In the preliminary screening experiments, strain F2 showed the highest efficiency in the removal of nitrite. Strain F2 was Gram-negative, non-motile, and had a short rod shape. The mature colonies of strain F2 were prominently aqua, rugose, round, humid, translucent, and irregularly bordered. A portion of the 16S rRNA sequence of strain F2 was obtained by polymerase chain reaction (PCR). A homology search using Blast showed that strain F2 was most closely related to Pseudomonas stutzeri P3 and P. stutzeri HD4−1. Therefore, strain F2 was identified as P. stutzeri F2. Based on the adjoint method and Gen-Bank database, a phylogenetic tree was established ( Figure 2).

Analysis of the Results of Targeted Domestication
The nitrite tolerance of strain F2 was domesticated by the concentration gradient increment method. Before domestication, strain F2 was able to grow to a maximum OD600 of only 1.12 in a denitrification medium with an initial NO2 − -N concentration of 300 mg/L ( Figure 3A), while at an initial nitrosomal nitrogen concentration of 500 mg/L, strain F2 barely grew. After a period of domestication, the growth of the strain improved significantly, and the corresponding maximum OD600 was 2.38, 1.91, and 1.41 at initial NO2 − -N concentrations of 300, 400, and 500 mg/L, respectively, indicating that the domesticated F2 strain has significantly increased tolerance to NO2 − -N and can be applied to the treatment of nitrite wastewater at high concentrations.

Analysis of the Results of Targeted Domestication
The nitrite tolerance of strain F2 was domesticated by the concentration gradient increment method. Before domestication, strain F2 was able to grow to a maximum OD 600 of only 1.12 in a denitrification medium with an initial NO 2 − -N concentration of 300 mg/L ( Figure 3A), while at an initial nitrosomal nitrogen concentration of 500 mg/L, strain F2 barely grew. After a period of domestication, the growth of the strain improved significantly, and the corresponding maximum OD 600 was 2.38, 1.91, and 1.41 at initial NO 2 − -N concentrations of 300, 400, and 500 mg/L, respectively, indicating that the domesticated F2 strain has significantly increased tolerance to NO 2 − -N and can be applied to the treatment of nitrite wastewater at high concentrations.

Aerobic Denitrification
The growth of cells of strain F2 was determined by fitting OD 600 with the

Aerobic Denitrification
The growth of cells of strain F2 was determined by fitting OD600 with the Slogistic1 equation, y(t) = a/{1 + exp[−k × (t − tc)]}. The coefficient of correlation (R2) was 0.99, indicating that the Slogistic1 equation sufficiently described the growth of strain F2 ( Figure  4). The results of the Origin 2020 analysis showed that the values of a, k, and tc were 1.09, 0.25, and 12.89, respectively. The removal efficiency of NO2 − -N reached 76.92% in 36 h with an initial concentration of about 300 mg/L. Nitrogen balance revealed that 6.1% of the initial NO2 − -N was used for cell synthesis, and 71.29% was converted to gaseous nitrogen ( Table 1). The production of gaseous nitrogen was similar to that of P. stutzeri XL−2 [15], which also indicated that the F2 strain did undergo aerobic denitrification.

Aerobic Denitrification
The growth of cells of strain F2 was determined by fitting OD600 with the Slogistic1 equation, y(t) = a/{1 + exp[−k × (t − tc)]}. The coefficient of correlation (R2) was 0.99, indicating that the Slogistic1 equation sufficiently described the growth of strain F2 ( Figure  4). The results of the Origin 2020 analysis showed that the values of a, k, and tc were 1.09, 0.25, and 12.89, respectively. The removal efficiency of NO2 − -N reached 76.92% in 36 h with an initial concentration of about 300 mg/L. Nitrogen balance revealed that 6.1% of the initial NO2 − -N was used for cell synthesis, and 71.29% was converted to gaseous nitrogen ( Table 1). The production of gaseous nitrogen was similar to that of P. stutzeri XL−2 [15], which also indicated that the F2 strain did undergo aerobic denitrification.   The removal efficiency of NO 2 − -N reached 76.92% in 36 h with an initial concentration of about 300 mg/L. Nitrogen balance revealed that 6.1% of the initial NO 2 − -N was used for cell synthesis, and 71.29% was converted to gaseous nitrogen ( Table 1). The production of gaseous nitrogen was similar to that of P. stutzeri XL−2 [15], which also indicated that the F2 strain did undergo aerobic denitrification. The carbon source is one of the essential nutrients for microbial growth, providing the cellular carbon shelf for microbial growth and metabolism, and energy for cellular life activities. For aerobic denitrifying bacteria, the carbon source affects not only their growth but also their denitrification efficiency. This is because aerobic denitrification is a redox reaction, and the carbon source not only provides the energy required by the cells during the growth of the strain, but also provides the electron donor. Different carbon sources have different redox potentials and, therefore, different abilities to provide electrons, which can have an impact on the aerobic denitrification reaction. In addition, carbon sources also affect the activity of enzymes involved in aerobic denitrification [16,17]. The chemical structure and molecular weight of the carbon source were reported to have a significant effect on the denitrification efficiency, and the strains generally preferred to utilize carbon sources with simple chemical structures and small molecular weights, such as sodium succinate and sodium citrate [18,19].
To investigate the effects of different carbon sources on the growth and degradation of nitrite by strain F2, the initial NO 2 − -N concentration was fixed at about 300 mg/L, and sodium succinate, trisodium citrate, and maltose were selected as the carbon sources for the experiment. Strain F2 was able to grow better using sodium succinate and trisodium citrate, and when the carbon source was maltose, the growth efficiency of the strain was significantly reduced, which indicated that there were differences in the growth of strain F2 under different carbon sources. Among them, strain F2 grew most vigorously in sodium succinate with OD 600 of up to 2.03 ( Figure 5A), followed by trisodium citrate with OD 600 of up to 1.73; in the environment with maltose as the carbon source, the biomass of the strain was inhibited with a maximum of 0.65. In the case of sodium succinate and trisodium citrate as the carbon source, strain F2 entered the logarithmic phase relatively quickly. This may be because sodium succinate and citric acid have simple chemical structures and small molecular weights; on the other hand, succinate and citric acid are intermediate products of the tricarboxylic acid cycle and are more easily utilized by microflora. From Figure 5B,C, it can be seen that there is a consistency among the growth of strain F2, the degradation of NO 2 − -N and the removal of TN; the higher the density of OD 600 of the bacterial solution, the higher the degradation rate of NO 2 − -N and the removal rate of TN. The density of the bacterial solution with sodium succinate as the carbon source was significantly higher than that of the remaining two groups, and its NO 2 − -N degradation rate was 84.54% and TN removal rate was 78.41%, which was higher than those of the culture solution with trisodium citrate and maltose as the carbon source. During the experiment, the concentration of NO 3 − -N increased and then decreased as the incubation proceeded ( Figure 5D), and NH 4 + -N accumulated gradually over time, but the content was always at a low level ( Figure 5E). The experimental results indicate that the carbon source affects the nitrite removal rate of the bacteria by influencing their growth, and sodium succinate was used as the carbon source in all the following experiments.

C/N
The carbon to nitrogen ratio has a great effect on the metabolism of substances and energy in bacteria [20]. Under different carbon to nitrogen ratio conditions, the denitrification ability of the strain is different. The concentration of the carbon source will directly affect the growth and aerobic denitrification performance of the strain. When the carbon source is insufficient, it will result in providing less and slower electron flow to support the growth of the strain; then, accordingly, the efficiency of aerobic denitrification will be reduced. However, when the level of the carbon source is too high, it becomes a non-limiting factor, and the growth and metabolism of the strain reach stability [21].
To investigate the effect of organic carbon source concentration on the growth and denitrification efficiency of strain F2, the initial NO 2 − -N was fixed at about 300 mg/L, and the initial organic carbon concentration was changed to control the carbon to nitrogen mass ratio of 6, 12, and 18. When the C/N ratio was 6, the maximum OD 600 of the bacterium was only 1.71 ( Figure 6A) and the nitroso-nitrogen degradation rate was 66.33%. When the C/N increased to 12, the biomass of the bacterium increased significantly and was in the late logarithmic growth stage. The nitroso-nitrogen denitrification rate reached 84.47%, and the NO 2 − -N removal efficiency was higher. When the C/N ratio increased from 12 to 18, there was a slight increase in the biomass of F2. The change was not particularly prominent, and almost all NO 2 − -N nitrogen sources could be effectively reduced. In addition, nitrate-N and ammonia-N were gradually detected after 6 h of inoculation, and the concentration of nitrate-N reached its peak at 18 h. With the increase in fermentation time, the concentration of nitrate-N gradually decreased and was always below 10 mg/L in all groups ( Figure 6D). The concentration of ammonia nitrogen exhibited an increasing trend in the first 36 h and still showed a small inward increase at 36 h. Then, we continued to monitor the medium for an extended period of time and found that the content of NH 4 + -N gradually began to decrease after 36 h, which kept the concentration of NH 4 + -N at a low level ( Figure 6E). In addition, Roberson et al. [6] also confirmed that the higher the concentration of the carbon source as an energy source in a certain concentration range, the faster the aerobic denitrification rate, which is consistent with the results of this study. In the following experiments, C/N conditions were all controlled to 18.

C/N
The carbon to nitrogen ratio has a great effect on the metabolism of substances and energy in bacteria [20]. Under different carbon to nitrogen ratio conditions, the denitrification ability of the strain is different. The concentration of the carbon source will directly affect the growth and aerobic denitrification performance of the strain. When the carbon source is insufficient, it will result in providing less and slower electron flow to support the growth of the strain; then, accordingly, the efficiency of aerobic denitrification will be reduced. However, when the level of the carbon source is too high, it becomes a non-

pH
pH is an essential factor affecting microbial enzymatic activity, and most aerobic denitrifying strains prefer neutral to alkaline conditions. Low or high pH will affect the stability and charged state of enzymes and inhibit enzymatic activity. Low or high pH will also lead to hydrolysis and degradation of proteins and nucleic acids on the surface of microorganisms, affecting the uptake of nutrients by microorganisms and thus inhibiting their growth and metabolism [22,23].
To investigate the effect of pH on the growth and denitrification efficiency of strain F2, the initial NO 2 − -N concentration was determined by fixing it at about 300 mg/L, and the initial pH of the medium was set to 6.4. Strain F2 grew well in the medium with initial pH values of 7.2 and 8, and both achieved more than 90% degradation of nitroso-nitrogen, while it barely grew in the medium with an initial pH of 6.4 ( Figure 7A). At pH 7.2 and 8, as seen in Figure 8D,E, the pattern of variation of NO 3 − -N and NH 4 + -N was similar to that in previous experiments with no significant changes.
The experimental results indicate that strain F2 is suitable for growth and aerobic denitrification in neutral and alkaline environments, which is similar to Acinetobacter sp. HNR [24]. In reality, the pH of aquaculture water is generally neutral and alkaline, which indicates that strain F2 can be used practically and has a high commercial value. The following experimental medium pH was set to 8.

Temperature
Temperature affects the growth and enzymatic reactions of microorganisms and directly determines the efficiency of denitrification. Usually, high temperature leads to the denaturation of nucleic acids or proteins in the strain, while low temperature inhibits enzymatic activity, thus reducing the metabolic activity of denitrifying bacteria and leading to failure of nitrite reduction [25,26].
It was seen that the growth of strain F2 became slow at 36 °C ( Figure 8A), and the ability to degrade nitrite nitrogen appeared to decrease, indicating that high temperature and no significant differences were found. This was similar to P. stutzeri ZF31 [27] and Pseudomonas mendocina GL6 [28]. The strain F2 still had better growth and no obvious reduction in the ability to degrade nitrite nitrogen at 20 °C, indicating that the strain can perform some degree of denitrification at low temperatures, which is similar to Acinetobacter sp. HA2 [29]. These results show that strain F2 has great potential for application in wastewater treatment and aquaculture, and the suitable temperature range for denitrification of strain F2 is consistent with the temperature variation range of aquaculture water.

Temperature
Temperature affects the growth and enzymatic reactions of microorganisms and directly determines the efficiency of denitrification. Usually, high temperature leads to the denaturation of nucleic acids or proteins in the strain, while low temperature inhibits enzymatic activity, thus reducing the metabolic activity of denitrifying bacteria and leading to failure of nitrite reduction [25,26].
It was seen that the growth of strain F2 became slow at 36 • C ( Figure 8A), and the ability to degrade nitrite nitrogen appeared to decrease, indicating that high temperature was not conducive to the growth of the strain and its denitrification. The reason for this phenomenon may be that high temperature has a destructive effect on nitrite reductase, so the denitrification efficiency of strain F2 was somewhat inhibited. At 20 • C and 28 • C, the strain could grow well and degrade nitrite nitrogen by aerobic denitrification. The denitrifi-cation efficiency of strain F2 was significantly higher at 28 • C than at other temperatures, so the optimum temperature of strain F2 should be judged to be around 28 • C. At this time, the denitrification rate of strain F2 for nitrite nitrogen reached 92.54% ( Figure 8F). The degradation of other nitrogen sources was similar to the previous phenomena, and no significant differences were found. This was similar to P. stutzeri ZF31 [27] and Pseudomonas mendocina GL6 [28]. The strain F2 still had better growth and no obvious reduction in the ability to degrade nitrite nitrogen at 20 • C, indicating that the strain can perform some degree of denitrification at low temperatures, which is similar to Acinetobacter sp. HA2 [29]. These results show that strain F2 has great potential for application in wastewater treatment and aquaculture, and the suitable temperature range for denitrification of strain F2 is consistent with the temperature variation range of aquaculture water.

Dissolved Oxygen (DO)
Dissolved oxygen affects the aerobic denitrification reaction process through the inhibition of denitrifying enzyme synthesis, activity, or competition with nitrate for electron donors and is essential for bacterial denitrification performance [30]. The concentration of DO directly affects the growth and denitrification activity of aerobic denitrifying bacteria, and the aerobic denitrification mechanism varies greatly among strains. Therefore, further studies are necessary [9]. In this work, the concentration of dissolved oxygen in the medium was altered by regulating the shaker speed, and the concentration of dissolved oxygen increased with the increase in the shaker speed. When the shaker speed was 150 rpm, the DO level in the culture medium was measured to be about 7 mg/L, and the DO content increased by 1 mg/L for every 30 rpm of shaker speed.
The experimental results indicate that the dissolved oxygen threshold of strain F2 is extremely high, which indicates that the strain has a high tolerance to oxygen; that is, it still shows good denitrification ability under high dissolved oxygen conditions. The increase in DO content did not significantly increase the biomass, but the denitrification performance of strain F2 was significantly improved, with a nitrite nitrogen removal rate up to 98.67% and a total nitrogen removal rate reaching 95.69% ( Figure 9F). The degradation rate of nitrite nitrogen was improved compared to the previous degradation rate, and the change in ammonia nitrogen level was not very obvious.
In aquaculture, dissolved oxygen in the culture water is generally maintained between 4 and 8 mg/L, and according to the reported aerobic denitrifying bacteria, some strains are poorly tolerant to dissolved oxygen in the water column and have low denitrification efficiency [9]. Therefore, the aerobic denitrifying strain P. stutzeri F2 was screened in this research and still had a high denitrification rate under the dissolved oxygen condition of 9 mg/L, which shows a good prospect for the degradation of nitrite nitrogen under aerobic conditions.

Media
The basic denitrification medium (DM) [31] with the following composition (/L) was used in this study: 5.64g of Na3C6H5O7; 1.5g of KH2PO4; 0.42g of Na2HPO4; 0.1g of MgSO4·7H2O; 1.5g of NaNO2; pH was adjusted to 7. DM medium was used for bacterial enrichment, isolation, and shake flask fermentation production experiments, and agar plates were prepared from DM containing 20 g of agar per liter. All media were autoclaved at 121 °C for 30 min before use. The reagent quality of the carbon and nitrogen sources was varied according to the experimental needs, all reagents are from Aladdin Reagent (Shanghai, China) Co.

Media
The basic denitrification medium (DM) [31] with the following composition (/L) was used in this study: 5.64 g of Na 3 C 6 H 5 O 7 ; 1.5 g of KH 2 PO 4 ; 0.42 g of Na 2 HPO 4 ; 0.1 g of MgSO 4 ·7H 2 O; 1.5 g of NaNO 2 ; pH was adjusted to 7. DM medium was used for bacterial enrichment, isolation, and shake flask fermentation production experiments, and agar plates were prepared from DM containing 20 g of agar per liter. All media were autoclaved at 121 • C for 30 min before use. The reagent quality of the carbon and nitrogen sources was varied according to the experimental needs, all reagents are from Aladdin Reagent (Shanghai, China) Co.

Strain Screening and Identification
First, 5 mL of fresh sludge (Fujian DBN Aquatic Science and Technology Group CO., Zhangzhou, China) from the bottom of the aquaculture pond was transferred to a 250 mL conical flask with 100 mL of sterile water, glass beads were added, and the activated sludge was dispersed at 28 • C and 150 rpm shaking speed for 1 h. Then, the suspension in the 1 mL conical flask was transferred to a 250 mL conical flask containing 100 mL DM culture medium and incubated at 28 • C and 150 rpm with shaking for 36 h. After repeating enrichment three times, the suspension was picked up with an inoculating ring and scribed on a DM plate. After repeating isolation and purification three times, individual colonies were selected and inoculated in DM medium and incubated at 28 • C and 150 rpm under fermentation conditions. The removal efficiency of NO 2 − -N and TN in DM was measured separately to determine the aerobic denitrification ability of the isolates. Finally, 10 purified strains with aerobic denitrification ability were obtained by repeated delineation and determination of aerobic denitrification ability, and these strains were numbered F1−F10, then stored in storage tubes containing 50% glycerol in a −40 • C refrigerator. The strain with the highest TN removal rate was named F2.
The 16S rRNA gene of strain F2 was amplified using universal primer 27F/1492R, and the amplification was completed. The sequences were analyzed and compared in the NCBI database, and 16S rRNA gene sequences of closely related species within the same genus were selected to construct a phylogenetic tree using MEGA (version 7.0, Mega Limited, Auckland, New Zealand) software.

Targeted Domestication of Strains and Detection of Nitrogen Reduction
Bacteria were dipped from the bailout tubes with an inoculating loop, graded and delineated on LB plates, and incubated in an inverted incubator at 28 • C. After clear colonies grew, individual colonies were picked out and inoculated into a 50 mL conical flask containing 10 mL LB medium and incubated for 12 h at 28 • C and 150 rpm with shaking. Furthermore, 6% of the bacterial solution washed with sterile saline was inoculated into NO 2 − -N denitrification medium at a concentration of 300 mg/L in a 250 mL conical shaker containing 50 mL of liquid for 24 h. Then, 6% of the bacterial solution was inoculated into the next NO 2 − -N concentration of 300 mg/L fresh denitrification medium. Each concentration cycle was transferred several times until the strain F2 adapted to this concentration environment. Through several pre-experiments, the NO 2 − -N concentration was gradually increased and finally determined so that the F2 strain in the NO 2 − -N concentration of 500 mg/L DM medium growth OD 600 reached above 1, and the domestication was stopped. The strains were preserved, and the domesticated mutant strains were used for the later nitrogen reduction performance tests. To evaluate the aerobic nitrite removal capacity, growth (OD 600 ), NO 2 − -N, TN, NO 3 − -N, and NH 4 + -N indicators were measured by regular sampling.

Single Factor Affecting Aerobic Denitrification
An inoculation loop was used to dip the bacteria from the preserved strain tube in to the LB plate for graded delineation. This was incubated upside down in at 28 • C until a clear single colony was grown. A single colony was placed into a 50 mL conical flask with 10 mL LB culture medium, incubated at 28 • C, with 150 rpm shaker activation for 12 h. Then, 6% of the bacterial solution washed with sterile saline was inoculated into a 50 mL DM culture medium in a 250 mL conical flask. The culture conditions were 28 • C and 150 rpm, while the culture solution C/N mass ratio was adjusted to 10:1 when different carbon sources were explored. Other conditions were explored, and only the exploration conditions were changed. The OD 600 was sampled periodically, and the concentrations of TN, NO 2 − -N, NO 3 − -N, and NH 4 + -N in the supernatant were measured.

Analytical Methods
The absorbance (A) of the bacterial growth was determined by the absorbance method using the absorbance values, which were measured at 600 nm. The determination of NO 3 − -N, NH 4 + -N, and NO 2 − -N was carried out according to the literature. pH values were determined using a Mettler Toledo Delta 320 pH meter (Mettler-Toledo, Schwerzenbach, Switzerland). Intracellular N was estimated by multiplying biomass with the nitrogen percentage in biomass [32,33]. The nitrogen percentage in the biomass was estimated by C 5 H 7 NO 2 . Organic N, which is mainly released from the bacterial decay or extracellular materials, was calculated by subtracting final NO 3 − -N, NO 2 − -N, and NH 4 + -N from final TN. The initial nitrogen concentration was labeled TN 0 . Gaseous N was calculated by subtracting final TN and intracellular N from initial TN 0 . The concentration of organic N and gaseous N was calculated as follows:

Conclusions
Eventually, the most suitable conditions for each factor were selected, and the aquaculture wastewater was treated in several simulations. Strain F2 has great potential for application in wastewater treatment and aquaculture. Generally, after 36 h of fermentation treatment, the removal rates of both NO 2 − -N and TN reached more than 98%, respectively, with the conversion rate of gaseous nitrogen reaching more than 70%, indicating that strain F2 has good prospects for practical application in reducing nitrogen sources in water bodies.