CN110655199A

CN110655199A - Method for treating ammonia nitrogen wastewater by using heterotrophic nitrification-aerobic denitrification pseudomonas strain

Info

Publication number: CN110655199A
Application number: CN201810694763.9A
Authority: CN
Inventors: 孙巍; 夏春雨; 洪维祎; 宋玉文; 杨雅玲; 苏全榕; 阙才英; 魏清斯; 易艳玲; 宋雅坚; 林美琴
Original assignee: Longyan University
Current assignee: Longyan University
Priority date: 2018-06-29
Filing date: 2018-06-29
Publication date: 2020-01-07
Anticipated expiration: 2038-06-29
Also published as: CN110655199B

Abstract

The invention discloses a method for treating ammonia nitrogen wastewater by using a heterotrophic nitrification-aerobic denitrification pseudomonas strain, wherein the ammonia nitrogen wastewater contains organic acid sodium, and the C/N ratio is 8-120, and the method comprises the following steps: inoculating the heterotrophic nitrification-aerobic denitrification pseudomonas seed liquid into ammonia nitrogen wastewater, and carrying out oscillation reaction for 6 h-7 d under the conditions that the temperature is 25-40 ℃ and the rotating speed is 90-180rpm, so as to finish the treatment of the ammonia nitrogen wastewater; the strain is pseudomonas LJ9, is preserved in Guangdong province microorganism strain preservation center, and has the preservation number of GDMCC NO: 60339. the strain LJ9 has high tolerance to wastewater with high C/N and high ammonia nitrogen concentration and high ammonia nitrogen removal rate, so the method has great application value in the aspect of removing ammonia nitrogen from wastewater with high carbon nitrogen ratio and high ammonia nitrogen concentration.

Description

Method for treating ammonia nitrogen wastewater by using heterotrophic nitrification-aerobic denitrification pseudomonas strain

Technical Field

The invention relates to the technical field of microorganisms, in particular to a method for treating ammonia nitrogen wastewater by utilizing a heterotrophic nitrification-aerobic denitrification pseudomonas strain.

Background

In recent years, the problem of water pollution is increasingly severe, nitrogen is an important pollution factor in water, excessive nitrogen flows into water, water eutrophication is easily caused, insufficient dissolved oxygen in water is caused, water quality is deteriorated, the ecological environment of the water is changed, the survival of aquatic organisms is damaged, and the pollution to the environment and the health of human beings is extremely large. Nitrogen exists in water in two forms of organic nitrogen and inorganic nitrogen, and the main source of the organic nitrogen is domestic sewage, agricultural nitrogen fertilizer and industrial wastewater; inorganic nitrogen is decomposed and converted by microorganisms and mainly comprises ammonia nitrogen, nitrate nitrogen and nitrite nitrogen, wherein the nitrate nitrogen can be converted into the nitrite nitrogen in a human body, and the nitrite is excessively taken, so that the methemoglobinemia is induced, and the suffocation is caused in serious cases. Nitrate-containing foods and water are more dangerous to infants and can lead to blue infants.

The problem of nitrogen pollution of the environmental water body is solved. Because the biological denitrification treatment has low cost and no secondary pollution to the environment, the biological denitrification treatment is the most common pollution at presentOne of the water denitrification methods is receiving attention at home and abroad. The conventional biological denitrification process is mainly based on Nitrification (NH) of autotrophic microorganisms under aerobic conditions₄ ⁺→NH₂OH→NO₂ ^-→NO₃ ^-) And denitrification of heterotrophic microorganisms under anaerobic conditions (NO)₃ ^-→NO₂ ^-→NO→N₂O→N₂). In the technology, autotrophic bacteria and heterotrophic bacteria need to be utilized, the autotrophic bacteria grow slowly by taking an inorganic carbon source as a raw material and have strong environmental sensitivity, and the heterotrophic bacteria need a large amount of organic matters for growth and have high energy consumption. Because of different nutrient substances and growth conditions in the nitrification and denitrification processes, large-scale equipment is needed, the time is long, and the theoretical denitrification efficiency is low. 1983, Robertson and the like firstly discover Heterotrophic Nitrification-aerobic denitrification bacteria Paracoccus, and put forward the concept of Heterotrophic Nitrification-aerobic denitrification (HN-AD) process, break through the traditional biological denitrification concept, and the novel biological denitrification technology is developed along with the situation. Compared with the traditional ammoniation, nitrification and denitrification, the novel denitrification technology simplifies the process flow, and the nitrification and denitrification are synchronously carried out in the same reactor under the aerobic condition. The bacteria grow and propagate quickly, and have higher denitrification efficiency, simple operation and more economical and practical. Therefore, the development of novel efficient denitrification heterotrophic nitrification-aerobic denitrification bacteria separation screening and denitrification performance research becomes a research focus at present.

In recent years, successively learners have screened out some of HN-AD (NH)₄ ⁺→NH₂OH→NO₂ ^-→NO→N₂O→N₂) The strain of (1). The HN-AD bacteria have wide substrate utilization range, can utilize various inorganic nitrogen and organic nitrogen, and have strong environmental adaptability. However, the HN-AD strain disclosed at present has poor high carbon nitrogen ratio resistance and high-concentration nitrogen resistance, and restricts the practical application and popularization of the heterotrophic nitrification-aerobic denitrification biological nitrogen removal technology in water body pollution remediation.

Disclosure of Invention

The invention aims to overcome the defects of the prior art and provides a method for treating high-carbon-nitrogen-ratio and high-concentration ammonia nitrogen wastewater by using a heterotrophic nitrification-aerobic denitrification pseudomonas strain LJ 9.

In order to solve the technical problems, the invention adopts the following technical scheme:

a method for treating ammonia nitrogen wastewater by using heterotrophic nitrification-aerobic denitrification pseudomonas strains comprises organic sodium, wherein the C/N ratio of the ammonia nitrogen wastewater is 8-120, and the method comprises the following steps:

inoculating the heterotrophic nitrification-aerobic denitrification pseudomonas seed liquid into ammonia nitrogen wastewater, and carrying out oscillation reaction for 6 h-7 d under the conditions that the temperature is 25-40 ℃ and the rotating speed is 90-180rpm, so as to finish the treatment of the ammonia nitrogen wastewater;

the strain is Pseudomonas LJ9(Pseudomonas indoxydans LJ9), is preserved in Guangdong province microbial strain preservation center, has the preservation time of 3 months and 21 days in 2018, and has the preservation number of GDMCC NO: 60339.

in one embodiment, the concentration of the ammonia nitrogen in the ammonia nitrogen wastewater is 100 mg-L^-1～500mg·L^-1。

In one embodiment, the C/N ratio of the ammonia nitrogen wastewater is 8-100, and the concentration of the ammonia nitrogen is 100 mg.L^-1～400mg·L^-1。

In one embodiment, the inoculation amount of the heterotrophic nitrification-aerobic denitrification pseudomonas seed liquid is 3% -5%.

In one embodiment, the pH value of the ammonia nitrogen wastewater is 6-9.

In one embodiment, the sodium organic acid is one or more of sodium citrate, sodium succinate and sodium acetate.

In one embodiment, the heterotrophic nitrification-aerobic denitrification pseudomonas seed liquid is prepared by the following method:

inoculating pseudomonas strain LJ9 into LB culture medium, culturing to logarithmic phase, centrifuging the obtained bacterial suspension to remove supernatant, washing, and adding sterile water to obtain pseudomonas seed liquid.

In one embodiment, the culturing process comprises: performing shaking culture at 25-35 ℃ and 100-180 rpm for 12-18 h.

In one embodiment, the LB medium comprises: bacteriological peptone 10 g.L^-15 g.L yeast extract^-1，NaCl 10g·L^-1，pH 7.0。

In one embodiment, sterile water is added to the bacterial liquid OD₆₀₀0.6 to 0.8.

Compared with the prior art, the invention has the advantages that:

the invention utilizes seed liquid obtained by culturing Pseudomonas strain LJ9 to treat ammonia nitrogen wastewater, Pseudomonas LJ9(Pseudomonas indoxydans LJ9) has the capability of tolerating high-concentration organic matters, ammonia nitrogen, nitrate nitrogen and nitrite nitrogen. In the heterotrophic nitrification process, the carbon source is sodium citrate, and the ammonia nitrogen concentration is 100 mg.L^-1C/N is 75, pH value is 7.0, inoculum size is 3%, the strain is cultured in a shaker at 25 ℃ for 24h at the rotating speed of 180rpm, the removal rate of ammonia nitrogen of the strain LJ9 reaches more than 90%, almost no accumulation of nitrite nitrogen and nitrate nitrogen exists, and when the concentration of ammonia nitrogen is 400 mg.L^-1The ammonia nitrogen removal rate can reach 99.49 percent within 7 days, and the ammonia nitrogen concentration reaches 500 mg.L^-1Can still remove ammonia nitrogen, and the bacterial strain LJ9 has wider application range to C/N, and the ammonia nitrogen concentration is 100 mg.L^-1And when the C/N is 8-120, the ammonia nitrogen removal rate of LJ9 reaches more than 80%. The strain LJ9 has high tolerance to wastewater with high C/N and high ammonia nitrogen concentration and high ammonia nitrogen removal rate, so that the pseudomonas strain LJ9 has great application value in the aspect of treating wastewater with high carbon nitrogen ratio and high ammonia nitrogen concentration, and particularly has the advantages and potential of ammonia nitrogen removal treatment of high-concentration citric acid wastewater.

In addition, the nitrate nitrogen concentration of the strain LJ9 in the aerobic denitrification process is 100 mg.L^-1C/N is 25-75, and the removal rate of nitrate nitrogen in 24 hours reaches more than 99 percent; compared with most aerobic denitrifying bacteria, the strain LJ9 has the capability of tolerating higher C/N, and the strain LJ9 can tolerate the nitrate nitrogen concentration as high as 600 mg.L^-1And 24h nitrate nitrogen removalThe removal rate can reach 90.05 percent, which shows that the influence of nitrate inhibition on the aerobic denitrification reaction process of LJ9 is small, and the aerobic denitrification performance of the strain is superior to that of most aerobic denitrification strains reported at present. In the aerobic nitrosation process, the nitrogen concentration of nitrite is 100 mg.L^-1When the C/N is 8-25, the removal rate of nitrite nitrogen of the strain LJ9 is more than 55%, and the strain LJ9 can tolerate the nitrite nitrogen concentration as high as 300 mg.L^-1Compared with most aerobic denitrifying bacteria, the strain LJ9 has the capability of tolerating higher C/N, and the strain LJ9 can tolerate nitrite nitrogen with higher concentration, so that the problem of nitrite accumulation can be solved more effectively, and the aerobic denitrification reaction process is not easy to be inhibited by nitrite.

Pseudomonas LJ9(Pseudomonas indoxydans LJ9) deposited in the microbial cultures Collection center of Guangdong province (GDMCC for short), and having the address of No. 59, No. 5, of Michelia furiosaefolia Miyao No. 100, Guangdong province, with the collection number of GDMCC NO: 60339, and the preservation time is 3 months and 21 days in 2018.

Drawings

FIG. 1 is a colony morphology of Pseudomonas LJ9 used in the present invention.

FIG. 2 is a transmission electron micrograph of Pseudomonas LJ9 used in the present invention.

FIG. 3 shows the 16S rRNAPCR electrophoretogram of Pseudomonas LJ9 used in the present invention.

FIG. 4 shows homology analysis of Pseudomonas LJ9 used in the present invention.

FIG. 5 is the electrophoresis picture of the pseudomonas LJ9 functional gene napA adopted by the invention.

FIG. 6 is a graph showing the growth and heterotrophic nitrification denitrification of Pseudomonas LJ9 used in the present invention.

FIG. 7 shows the effect of C/N on the heterotrophic nitrification denitrification performance of Pseudomonas LJ9 used in the present invention.

FIG. 8 shows the effect of different ammoniacal nitrogen concentrations on the growth of Pseudomonas LJ9 used in the present invention.

FIG. 9 shows the effect of different ammonia nitrogen concentrations on denitrification performance of Pseudomonas LJ9 used in the present invention.

FIG. 10 is a graph showing the effect of different carbon sources on the heterotrophic nitrification denitrification performance of Pseudomonas LJ9 used in the present invention.

FIG. 11 is a graph showing the effect of different pH values on the heterotrophic nitrification denitrification performance of Pseudomonas LJ9 used in the present invention.

FIG. 12 is a graph showing the effect of the inoculum size on the heterotrophic nitrification denitrification performance of Pseudomonas LJ9 used in the present invention.

FIG. 13 is a graph showing the effect of temperature on the heterotrophic nitrification denitrification performance of Pseudomonas LJ9 used in the present invention.

FIG. 14 is a graph showing the effect of dissolved oxygen on the heterotrophic nitrification denitrification performance of Pseudomonas LJ9 used in the present invention.

FIG. 15 is a graph showing growth and aerobic nitrosification denitrification curves of Pseudomonas LJ9 used in the present invention.

FIG. 16 is a graph showing the growth and aerobic denitrification curves of Pseudomonas LJ9 according to the present invention.

FIG. 17 shows the effect of different C/N on aerobic nitrous denitrification performance of Pseudomonas LJ9 used in the present invention.

FIG. 18 shows the effect of different C/N on the aerobic denitrification performance of Pseudomonas LJ9 used in the present invention.

FIG. 19 is a graph showing the effect of different nitrate nitrogen concentrations on the denitrification performance of Pseudomonas LJ9 used in the present invention.

FIG. 20 is a graph showing the effect of different nitrite nitrogen concentrations on the denitrification performance of Pseudomonas LJ9 used in the present invention.

Detailed Description

The invention is further described below with reference to specific preferred embodiments, without thereby limiting the scope of protection of the invention.

The heterotrophic nitrification-aerobic denitrification pseudomonas strain used in the following examples is deposited in the Guangdong province culture Collection (abbreviated as GDMCC) with the deposition number of GDMCC NO: 60339. The pseudomonas GDMCC NO: 60339 is named as Pseudomonas sp LJ9(Pseudomonas indoxydans LJ 9).

1) Separating, screening and purifying strains

The pseudomonas LJ9 of the embodiment is mainly obtained by screening through the following method:

1.1) enrichment culture: 50mL of activated sludge collected from Longjin sewage treatment plant in Longyan city, Fujian province is added into 100mL of DM culture medium, and 2-4 sterile glass beads are added into the culture medium at the same time, so as to break up a mud sample. The culture was continued at 30 ℃ for 5 days with shaking at 150 rpm. The above bacterial suspension was inoculated into a new DM medium at an inoculum size of 10%, and the culture was repeated twice in this manner to obtain an enriched bacterial suspension.

1.2) separation and purification: 0.2mL of the bacterial suspension was applied to a DM solid medium plate by 10-fold dilution and cultured in an incubator at 30 ℃. And (3) when a single colony grows out of the plate, selecting bacterial colonies with obviously different characteristics, and further carrying out plate streaking for many times to obtain a purified single colony.

1.3) primary screening: to determine the denitrifying power of the strains, the purified strains were cultured in KNO₃In DM solid medium plates, which are the sole nitrogen source, colonies that were able to grow on the plates were picked to complete the primary screening.

1.4) re-screening: the strains after primary screening are inoculated into a heterotrophic culture medium and a denitrification culture medium, and strains LJ9 with ammonia nitrogen and nitrate nitrogen degradation rates of 66% and 96% are screened out respectively.

1.5) preservation: the strain is preserved by adopting a method of slant preservation of beef extract peptone at 4 ℃ and low-temperature freezing preservation of glycerol suspension. The low-temperature freezing preservation method of the glycerol suspension comprises the following steps: mixing 50% glycerol distilled water with LB cultured strain suspension at a ratio of 1: 1, and storing at-80 deg.C with final concentration of glycerol of about 25%.

2) Strain identification

The identification process and the results of the pseudomonas LJ9 strain of the embodiment are as follows:

2.1) morphological identification

The isolated strains were observed for single colony morphology on solid plates. The shape of the thallus is observed by adopting a gram staining method and a transmission electron microscope.

Strain LJ9 was streaked on beef extract peptone agar medium for 48h as shown in FIG. 1: the large bacterial colony is round, neat, moist, smooth in surface, milky translucent, and small convex. Gram staining identifies the bacterium as gram negative. The strain morphology is shown in the transmission electron microscope image of FIG. 2: the cells were rod-shaped, 6X 12.5 μm in size, flagellated, and sporulated.

2.2) physiological and biochemical identification

The typical method for classifying bacteria in detail is based on the results of physiological and biochemical experiments of bacteria, and the physiological and biochemical characteristics of the strains in the experiments are identified according to the handbook for identifying common bacteria systems and the handbook for identifying Bergeming bacteria.

The strain LJ9 is subjected to various physiological and biochemical characteristics, and the results are shown in Table 1: LJ9 can survive under anaerobic and aerobic conditions, oxidase, catalase, starch hydrolysis, methyl red, grease hydrolysis, citrate, indole experiments and nitrate reduction experiments are positive, and glucose oxidation fermentation, lactose oxidation fermentation, urea hydrolysis, V.P reaction, gelatin liquefaction, acetic acid oxidation, pectin hydrolysis, hydrogen sulfide production and pyocyanin experiments are negative. The above results show that: LJ9 has similar physiological and biochemical characteristics to Pseudomonas and can secrete a lot of extracellular enzymes, oxidize sugars, produce a small amount of acid and do not ferment.

TABLE 1 physiological and biochemical Properties of Strain LJ9

Name of experiment	Results of the experiment	Name of experiment	Results of the experiment
				Oxidase enzyme	+	Nitrate reduction	+
Contact enzyme	+	Pyocyancin	-
				Oxidative fermentation of glucose	-	Indole experiments	+
Lactose oxidative fermentation	-	Milk with litmus	+
				Hydrolysis of urea	-	Production of hydrogen sulfide	-
Starch hydrolysis	+	Citric acid salt	+
				Methyl Red	+	Pectin hydrolysis	-
V.P	-	Oxidation of acetic acid	-
				Hydrolysis of fats and oils	+	Liquefaction of gelatin	-
With paraffin seal (without oxygen)	+	Paraffin-free seal (aerobic)	+

Note: in Table 3, "+" indicates positive, there was a reaction; "-" indicates negative, no such reaction. In the sugar fermentation experiment, "+" indicates no production of acid or gas; "-" indicates no acid or gas production.

2.3) molecular biological identification

The bacterium contains three kinds of ribosomal RNA, 5S rRNA, 16S rRNA and 23S rRNA. rRNA gene consists of conserved region and variable region, and has moderate relative molecular weight and high repeatability of sequence analysis. Therefore, it is now common to use the 16S rRNA gene as a target for sequence analysis to perform sequencing analysis of microorganisms for determining the species of bacteria.

2.3.1) extraction of bacterial genomic DNA

Extracting the bacterial genome DNA by using an Ezup column type bacterial genome DNA extraction kit and operating according to the specific operation steps of the kit.

Extracting strain DNA as PCR template for amplification. The primers are universal primers, namely upstream 27F:

5'-AGAGTTTGATCCTGGCTCAG-3', downstream 1492R:5'-GGTTACCTTGTTACGACTT-3', reacted in a PCR amplificator.

2.3.2) amplification and sequencing of the 16S rRNA Gene

PCR amplification System (Total 25. mu.l): 10 XBuffer 2.5. mu.l, dNTP 0.5. mu.l, 27F 0.5. mu.l, 1492R 0.5. mu.l, template DNA 1. mu.l, Taq enzyme 0.25. mu.l, sterile water 19.75. mu.l.

The PCR reaction program settings are shown in table 2:

TABLE 2

Pre-denaturation	95℃	3min
			Denaturation of the material	95℃	45s
Annealing	55℃	45s
			Extension of	72℃	45s

In total 35 cycles were run, with the 35 th cycle being extended for 5min at 72 ℃. Storing at 4 ℃.

And after the PCR product is qualified through agarose gel electrophoresis detection, committing Shanghai Huada Gene company to complete sequence determination, and performing homology analysis on a sequencing result to obtain the phylogenetic position of the strain.

The result of agarose gel electrophoresis imaging of the PCR amplification product of the rRNA gene of strain LJ916S is shown in FIG. 3: the PCR product band is bright, the channel has no impurities, and the band position is above 1000bp, which indicates that the 16S rRNA gene target band is obtained. The 16S rRNA gene PCR product of strain LJ9 was purified and sequenced to obtain a sequence of 1362bp in length, and the results of homology analysis by BLAST are shown in fig. 4: the strain LJ9 has 99% similarity with the strain Pseudomonas indoloxydans and is named as Pseudomonas indoloxydans LJ 9.

2.3.3) amplification of NapA functional Gene

Nitrate reductases are classified into membrane-bound nitrate reductases (Nar) and periplasmic nitrate reductases (Nap), in which periplasmic nitrate reductase genes are preferentially expressed under aerobic conditions and function under both anaerobic and aerobic conditions. Using primer nap 1: 5 '-TCTGGACCATGG-GCTTCAACCA-3', nap2: 5'-ACGACGACCGGCCAGCGCAG-3', and carrying out amplification on a PCR instrument.

PCR amplification System (Total 25. mu.l): 10 XBuffer 2.5. mu.l, dNTP 0.5. mu.l, nap 10.5. mu.l, nap 20.5. mu.l, template DNA 1. mu.l, Taq enzyme 0.25. mu.l, sterile water to 25. mu.l.

The PCR reaction program settings are shown in table 3:

TABLE 3

Pre-denaturation	94℃	10min
			Denaturation of the material	94℃	1min
Annealing	55℃	1min
			Extension of	72℃	1.5min

A total of 30 cycles were run, with the 30 th cycle being extended for a further 10min at 72 ℃. Storing at 4 ℃.

And (3) carrying out 1% agarose gel electrophoresis detection on the PCR product, carrying out electrophoresis for 30min at a voltage of 220V, and carrying out imaging photographing by a gel imaging system.

The primer nap1/nap2 is used for amplifying the periplasmic nitrate reductase gene of the LJ9 strain, and an agarose gel electrophoresis chart is shown in FIG. 5: the target band is between 750bp and 1000 bp. The napA genes of periplasmic nitrate reductase subunits are all about 870bp, so that the primary judgment can be made that the LJ9 contains the napA gene, which indicates that the strain LJ9 has the aerobic denitrification function.

The pseudomonas LJ9 of the embodiment has good heterotrophic nitrification-aerobic denitrification performance, has high carbon nitrogen ratio resistance and high nitrate nitrogen and nitrite nitrogen resistance, and can be used for denitrification treatment of wastewater with high C/N ratio, high nitrate nitrogen and high nitrite nitrogen. When the method is used, the pseudomonas LJ9 is prepared into pseudomonas LJ9 seed liquid, and then the wastewater denitrification treatment is carried out, wherein the pseudomonas LJ9 seed liquid is prepared by adopting the following method:

activating the strain LJ9 in an LB culture medium, culturing to a logarithmic phase, taking a strain suspension at 4000rpm, centrifuging for 10min, removing a supernatant, washing with sterile water, centrifuging again to remove the supernatant, repeating for 2-3 times, and adjusting the OD600 of the strain to 0.6-0.8 with sterile water to be used as a seed solution.

The formula of the culture medium used is as follows:

denitrification enrichment medium (DM) (g.L)^-1)：Na₂HPO₄·7H₂O 7.9，KH₂PO₄1.5，NH₄Cl 0.3，MgSO₄·7H₂O0.1, sodium succinate (CH)₂COONa)₂·6H₂O 4.7，KNO₃0.3, 2 mL. L of trace element solution^-1，pH7.0-7.5。

Solution of trace elements (g.L)^-1)：EDTA50，ZnSO₄2.2，CaCl 5.5，MnCl₂·4H₂O 5.1，FeSO₄·7H₂O5.0, ammonium molybdate (NH)₄)6Mo₇O₂₄·4H₂O 1.1，CuSO₄·5H₂O 1.6，CoCI₂·6H₂O 1.6，pH 7.0。

Beef extract peptone medium (g.L)^-1): bacteriology10 parts of peptone, 3 parts of beef extract, 10 parts of NaCl and 7.0-7.2 parts of pH.

LB liquid Medium (g.L)^-1): bacteriological peptone 10, yeast extract 5, NaCl 10, pH 7.0.

Heterotrophic nitrification medium (g.L)^-1)：(NH₄)2SO₄0.47, sodium succinate (CH)₂COONa)₂·6H₂O4.5, sodium citrate C₆H₅Na₃O₇·2H₂O3.27, Vickers salt solution 50 mL. L^-1，pH 7.0。

Vickers salt solution (g.L)^-1)：K₂HPO₄6.54，MgSO₄·7H₂O 2.5，NaCl 2.5，MnSO₄·H₂O 0.04，FeSO₄·7H₂O 0.05。

Denitrification Medium (g.L)^-1)：KNO₃0.72, sodium succinate (CH)₂COONa)₂·6H₂O4.5, (sodium citrate C)₆H₅Na₃O₇·2H₂O3.27), vickers' salt solution 50mL, pH 7.0.

Nitrosation medium (g.L)^-1)：NaNO₂0.49, sodium succinate (CH)₂COONa)₂·6H₂O4.5 (sodium citrate C)₆H₅Na₃O₇·2H₂O3.27), vickers' salt solution 50mL, pH 7.0.

Note: the solid culture medium is prepared by adding 1.5-2% of agar into the liquid culture medium, and sterilizing all the culture media at 121 ℃ for 20min for later use.

The experimental instruments used in the examples are shown in table 4:

TABLE 4 Experimental instruments

The water quality testing and analyzing items and methods in the examples are shown in table 5:

TABLE 5 items and methods for Water quality testing analysis

Index (I)	Measurement method
		Ammoniacal Nitrogen (NH)₄ ⁺-N)	Spectrophotometry with Nas reagent
Nitrate Nitrogen (NO)₃ ^--N)	Thymol spectrophotometry
		Nitrous Nitrogen (NO)₂ ^--N)	N- (1-naphthyl) -ethylenediamine photometry
Total Nitrogen (TN)	Alkaline potassium persulfate digestion spectrophotometer
		Chemical Oxygen Demand (COD)	COD instrument digestion method
pH	UB-7 precision pH meter
		Absorbance OD of biomass of bacteria₆₀₀	Measured at a wavelength of 600nm using an ultramicro spectrophotometer

Example 1:

a method for treating ammonia nitrogen wastewater by using the heterotrophic nitrification-aerobic denitrification pseudomonas strain LJ9 seed liquid comprises the following steps:

inoculating the seed liquid into triangular conical flasks (500 ml) containing 200ml heterotrophic nitrification medium with 3% inoculation amount, with initial ammonia nitrogen concentration of 100 mg.L^-1C/N is 8, pH is 7.5, 30 ℃, 150rpm, shaking culture is carried out for 48 hours, samples are taken every 6 hours, and COD and NH are measured₄ ⁺-N、NO₂ ^--N、NO₃ ^-Content of-N and TN, and OD thereof₆₀₀And a pH value.

Research result of heterotrophic nitrification performance

The strain LJ9 takes sodium succinate as a carbon source and NH₄ ⁺N is the only nitrogen source, and the growth and heterotrophic denitrification curves after 48h of culture are shown in FIG. 6: the growth speed of the strain LJ9 is slow in 0-6h, which indicates that the adaptation period of the strain is about 6h, the strain grows rapidly in 6-18h, the logarithmic growth period is 18h, the biomass reaches the maximum, and the OD is OD₆₀₀At 0.502, after 18h, the strain enters a stationary growth phase due to the consumption of nutrients, the death rate of the strain is increased after 36h, and the biomass is reduced. Therefore, 18-24h is the optimal time for the strain to grow. The pH increased with time from the initial 6.66 to 7.94, indicating that the growth of strain LJ9 is alkaline producing.

The degradation rate of the strain LJ9 in 0-6h ammonia nitrogen is lower by 3.86%, and NO is simultaneously added₃ ^--N and NO₂ ^-The continuous accumulation of-N reaches 0.383 mg.L respectively^-1、0.408mg·L^-1. Ammonia nitrogen is rapidly degraded within 6-18 h; the ammonia nitrogen removal rate is close to 100% in 18h, and the total nitrogen removal rate reaches 82%; NO after 24h₃ ^--N is substantially not accumulated, NO₂ ^-The accumulated amount of-N is less, and the COD removal rate is basically in a stable state and reaches about 80 percent. After 36h, the strains slowly decline, the removal rate of ammonia nitrogen and total nitrogen is reduced, nitrogen is possibly produced due to the metabolism of bacterial cells, and ammonia nitrogen is possibly accumulated again. NH (NH)₄ ⁺The degradation curve of the-N is basically consistent with the growth curve of the strain, the ammonia nitrogen removal rate reaches the highest in 18h, the strain enters a stationary phase or a decline phase in 18h, cells are cracked, and the ammonia nitrogen content is increased. There is an accumulation of nitrite nitrogen and nitrate nitrogen, indicating that denitrification also occurs while heterotrophic nitrification is taking place.

Example 2:

ammonia nitrogen concentration 100 mg.L^-1Changing the content of carbon source, inoculating the seed liquid into heterotrophic nitrification culture medium with C/N ratio of 4, 8, 12, 16, 20, 25, 30, 35, 50, 75, 100, 120 and inoculation amount of 3%, respectively, using sodium citrate as carbon source,

pH

7, 30 deg.C, 150rpm, shake culturing for 24 hr, sampling and measuring NH₄ ⁺N, TN content and its pH and OD₆₀₀。

The results are shown in FIG. 7: the strain LJ9 has wide adaptation range to C/N, and the ammonia nitrogen removal rate of LJ9 reaches over 80 percent when the C/N is 8-120. Compared with most heterotrophic nitrification-aerobic denitrification bacteria reported at present, the growth and denitrification of LJ9 have high C/N resistance.

The high-concentration organic wastewater which is easy to be biodegraded can be divided into the following according to the property sources: industrial waste water, such as food industry waste water, etc. with farm and pasture products as raw materials; one is light industrial and metallurgical waste water, such as pharmaceutical waste water. Citric acid is the most important organic acid widely used in food, medicine, daily chemical and other industries. The embodiment shows that the strain LJ9 has high carbon-nitrogen resistance, so that the strain has good tolerance to high-concentration organic pollution, and has good denitrification effect by taking sodium citrate as a carbon source, which shows that the strain LJ9 has the advantages and potential of denitrification treatment of high-concentration citric acid wastewater.

Example 3:

inoculating the seed liquid with ammonia nitrogen concentration of 100, 200, 300, 400, 500 mg.L respectively at an inoculation amount of 3%^-1In the heterotrophic nitrification culture medium, sodium citrate is used as a carbon source, C/N is 50, pH is 7, temperature is 25 ℃, shaking table is continuously cultured for 7 days at 180rpm, sampling is carried out at regular time every day, NH is measured₄ ⁺Content of-N, NO₂ ^--N and NO₃ ^-Cumulative amount of-N, and its pH and OD₆₀₀. Selection of Biomass (OD)₆₀₀) The highest day was used for measuring the COD and TN contents.

Results of influence of ammonia nitrogen concentration on heterotrophic nitrification performance of LJ9

The strain LJ9 was cultured for 7 days at different initial ammonia nitrogen concentrations, and the growth curve is shown in FIG. 8: initial ammonia nitrogen concentration 100-400mg·L^-1OD of LJ9₆₀₀With the increase of the ammonia nitrogen content, the growth lag phase is prolonged, and when the ammonia nitrogen concentration is 500 mg.L^-1When the strain LJ9 does not grow basically, the concentration is the limit of the tolerance of the ammonia nitrogen of LJ9, but the ammonia nitrogen can be removed by LJ9 at the concentration. The initial ammonia nitrogen concentration is 200-400 mg.L^-1In time, by day 7 of culture, LJ9 growth was already in stationary phase, OD₆₀₀All reach about 1.3, so the range of ammonia nitrogen concentration tolerance for the growth of LJ9 is wider.

The results of the influence of different initial ammonia nitrogen concentrations on the denitrification performance of the strain LJ9 are shown in FIG. 9: after 7 days of culture, the removal rates of ammonia nitrogen of LJ9 are 91.29%, 94.50%, 98.27%, 99.49% and 17.47%, respectively. At the initial ammonia nitrogen concentration of 100-^-1In the range, the ammonia nitrogen removal rate is improved along with the increase of the initial ammonia nitrogen concentration, and a small amount of nitrate nitrogen is accumulated; at the initial ammonia nitrogen concentration of 100-300 mg.L^-1The total nitrogen removal rate is increased along with the increase of the initial ammonia nitrogen concentration, but the initial ammonia nitrogen concentration is 400 mg.L^-1In time, biomass, total nitrogen and COD all decreased, OD₆₀₀The total nitrogen and COD removal rates are respectively reduced to 1.211 and 79.16 percent and 49.91 percent, which shows that the over-high nitrogen concentration can inhibit the growth and denitrification performance of the bacteria, and the highest ammonia nitrogen tolerance concentration of the strain LJ9 is about 500 mg.L^-1。

Different bacteria have different tolerance to high ammonia nitrogen. Heterotrophic nitrification-aerobic denitrification bacteria Pseudomonas putida LY1 and Acinetobacter sp.HY2 with initial ammonia nitrogen concentration of 50 mg.L^-1The ammonia nitrogen removal efficiency is the highest, and is respectively 64% and 74%, and the ammonia nitrogen degradation rate is gradually reduced along with the increase of the ammonia nitrogen concentration. Sp YN3 of Acinetobacter sp.with the increase of initial ammonia nitrogen concentration, the lower the ammonia nitrogen removing ability, the initial ammonia nitrogen concentration increased to 200 mg.L within 1 day^-1In this case, denitrification reaction hardly occurred, and the initial ammonia nitrogen concentration was 150 mg.L^-1And the removal rate of the ammonia nitrogen is only 18.7 percent in 24 h. Compared with the strain, the initial ammonia nitrogen concentration is respectively 100, 200, 300, 400 and 500 mg.L^-1When the strain is cultured for 24 hours, the removal rates of ammonia nitrogen of the strain LJ9 are 87.86%, 41.55%, 9.37%, 8.69% and 10.38% respectively. Description of the inventionLJ9 has better tolerance to ammonia nitrogen concentration.

Example 4:

carbon source influence on heterotrophic nitrification performance of LJ9

Carbon sources are nutrients that constitute a source of the carbon skeleton in biological cells or metabolites. Common organic carbon sources include: organic acid, small molecular alcohol, saccharide, oil and fat and organic ester. Sodium succinate, sodium acetate and sodium citrate in organic acid, ethanol of low-carbon alcohol, and glucose and sucrose in sugar are selected as carbon sources in the experiment. The heterotrophic bacteria utilize exogenous organic matter as carbon source, and the autotrophic bacteria utilize CO₂And (3) selecting an inorganic carbon source-sodium bicarbonate as a control group to examine whether the bacteria are heterotrophic bacteria or not, wherein the inorganic carbon is used as a carbon source.

Replacing the C source in the heterotrophic nitrification culture medium by equimolar mass, keeping other components unchanged, and preparing culture media with different carbon sources. Inoculating the seed liquid into triangular conical flasks (250 ml) containing 100ml of heterotrophic nitrification culture medium with different carbon sources at 3% of inoculation amount, respectively, culturing for 24 hr at C/N of 50, pH of 7, 30 deg.C and 150rpm, sampling, and measuring NH₄ ⁺N, TN content and its pH and OD₆₀₀。

Carbon source influence on heterotrophic nitrification performance of LJ9

Different carbon source types influence the growth rate of heterotrophic nitrification-aerobic denitrification bacteria, thereby influencing the ammonia nitrogen degradation capability of the heterotrophic nitrification-aerobic denitrification bacteria. The results of the influence of different carbon sources on the heterotrophic nitrification denitrification performance of LJ9 are shown in FIG. 10: LJ9 uses sodium citrate, sodium succinate and sodium acetate as carbon source, OD₆₀₀Respectively 0.392, 0.359 and 0.338, the ammonia nitrogen removal rates respectively reach 87.61 percent, 77.85 percent and 60.27 percent, the total nitrogen removal rates respectively reach 86.90 percent, 77.77 percent and 60.77 percent, and the results show that when organic acid is used as a carbon source, the strain LJ9 has good denitrification effect and biomass (OD) is good₆₀₀) The ratio is higher; OD Using sodium bicarbonate as a carbon Source₆₀₀The degradation rate of the ammonia nitrogen is only 37.49%, which indicates that the strain LJ9 can utilize inorganic carbon source and has autotrophic nitrification capability, but the inorganic carbon source is not suitable for the growth of the strain LJ9 and the degradation of the ammonia nitrogen; compared with sucrose, the biomass of LJ9 is slightly 0.195 when glucose is used as a carbon sourceHigher than 0.184 for sucrose. Ethanol is used as a carbon source, and the biomass of LJ9 is hardly increased, which indicates that the strain LJ9 cannot utilize ethanol as the carbon source, and when saccharides and ethanol are used as the carbon source, the pH value is reduced to 3-4, which indicates that acid is produced in the growth process of the strain, and the growth of the thalli is influenced. In addition, when sucrose, glucose and ethanol are used as carbon sources, the removal rate of ammonia nitrogen of LJ9 is low, and the removal rate is 24.77%, 5.39% and 14.84% in sequence; the medium without carbon source was not degraded and the biomass was not increased, indicating that the growth of LJ9 requires a carbon source and that no carbon source could not grow. In conclusion, the selected organic acid carbon source is suitable for growth and denitrification of LJ9, wherein when sodium citrate is used as the carbon source, the biomass of LJ9 is the largest, and the removal rate of ammonia nitrogen and total nitrogen is the highest, so the sodium citrate is selected as the carbon source for researching the denitrification performance of LJ 9.

Example 5:

effect of pH on heterotrophic nitrification performance of LJ9

Inoculating 3% of the seed solution into heterotrophic nitrification culture medium with pH of 6.5, 7.0, 7.5, 8.0, 8.5, and 9.0, respectively, shake culturing for 24 hr with sodium citrate as carbon source, C/N of 50, pH of 7, 30 deg.C, and 150rpm, sampling, and measuring NH₄ ⁺N, TN content and its pH and OD₆₀₀。

Influence of pH on heterotrophic nitrification performance of LJ9

The growth of microorganisms has a certain pH tolerance range. The results of the influence of different initial pH values of the culture medium on the denitrification performance under the strain LJ9 are shown in FIG. 11: at pH 6.5, LJ9OD₆₀₀There was no increase, with an ammonia nitrogen removal of only 8.97%, indicating that LJ9 was not suitable for growth under acidic conditions. When the pH value is 7-8.5, the ammonia nitrogen removal rate of 24h of culture is over 90 percent, and the total nitrogen removal rate is over 80 percent, wherein when the pH value is 7, the ammonia nitrogen removal rate and the total nitrogen removal rate are the highest and respectively reach 94.21 percent and 89.69 percent. When the pH value is 9, the biomass of LJ9 is obviously reduced, and the removal rate of ammonia nitrogen and total nitrogen is reduced after 24 hours and is close to 80 percent, which shows that the neutral and weak alkaline conditions are more favorable for the growth and denitrification of the strain LJ 9.

Generally speaking, most heterotrophic nitrification-aerobic denitrification bacteria are suitable for growth and have a pH range of 6-9, which indicates that the bacteria are more beneficial to growth and denitrification in milder environments such as neutral, weak acid, weak base and the like.

Example 6:

effect of inoculum size on heterotrophic nitrification performance of LJ9

Inoculating the seed liquid into heterotrophic nitrification culture medium with the inoculum sizes of 3%, 5%, 7%, 10%, 12% and 15%, respectively, shake-culturing for 24 hours with sodium citrate as carbon source, C/N of 50, pH of 7, 30 ℃ and 150rpm, sampling and measuring NH₄ ⁺N, TN content and its pH and OD₆₀₀。

Results of influence of inoculation amount on heterotrophic nitrification performance of LJ9

The inoculation amount can directly influence the growth lag period and generation time of the thalli. The effect of different inoculum sizes on the denitrification performance of strain LJ9 is shown in FIG. 12: when the inoculation amount is 3%, 5%, 7% and 10%, the ammonia nitrogen removal rate of LJ9 is respectively 95.13%, 94.36%, 94.45% and 92.42%, the total nitrogen removal rate is respectively 93.57%, 94.89%, 85.05% and 83.46%, and the total nitrogen removal rate is obviously reduced when the inoculation amount is 7%. With increasing inoculum size, the pH tended to decrease, indicating that the cells metabolically produced acid. Different inoculum sizes, after 24h of culture, the thallus OD₆₀₀Relatively close, wherein the OD is 3% of the inoculum₆₀₀Maximum 0.438, and 15% inoculation OD₆₀₀A minimum of 0.376. The reason is that the larger the inoculation amount is, the shorter the time of the strain propagation reaching the peak is, the nutrient substances are consumed quickly and are easy to be competitively inhibited, the later-period nutrition can not meet the requirement of the growth of the thalli, and a large amount of thalli die. OD 24h due to 3% inoculum size₆₀₀The removal rate of ammonia nitrogen and the removal rate of ammonia nitrogen reach the maximum, the difference between the total nitrogen removal rate and the inoculation amount of 5 percent is not large, and the inoculation amount of 3 percent is selected as the optimal inoculation amount.

Example 7:

effect of temperature on heterotrophic nitrification performance of LJ9

Inoculating the seed solution into a heterotrophic culture medium with an inoculum size of 3%, culturing for 24 hr in a shaker at 25 deg.C, 30 deg.C, 35 deg.C, 40 deg.C and 150rpm at C/N of 50 and pH of 7, respectively, sampling and measuring NH₄ ⁺N, TN content and its pH and OD₆₀₀。

Influence of temperature on heterotrophic nitrification performance of LJ9

The low temperature can inhibit the activity of microbial enzyme, the high temperature can cause the denaturation and inactivation of protein or nucleic acid, and the proper temperature can lead the growth and reproduction of the microbe to be faster and the metabolism to be vigorous. The effect of temperature on the denitrification performance of strain LJ9 is shown in FIG. 13: the suitable temperature range of the growth and denitrification of the strain LJ9 is wide, and the OD is between 25 and 40 DEG C₆₀₀0.3-0.5, the removal rate of ammonia nitrogen is more than 90%, the removal rate of total nitrogen is more than 80%, and the OD of LJ9 is at 25 DEG C₆₀₀The maximum is 0.486, the removal of ammonia nitrogen and total nitrogen reaches 95.86 percent and 87.41 percent, and therefore, 25 ℃ is selected as the culture temperature of LJ 9.

Generally, the optimal growth and denitrification temperatures of different strains are different, but most heterotrophic nitrification-aerobic denitrification bacteria have wider temperature range for growth and denitrification and have stronger adaptability.

Example 8:

effect of dissolved oxygen on heterotrophic nitrification performance of LJ9

Inoculating the seed solution into a heterotrophic nitrification culture medium with the inoculation amount of 3%, taking sodium citrate as a carbon source, culturing for 24 hours in a shaker at the temperature of 25 ℃ at the rotating speeds of 90rpm, 150rpm and 180rpm respectively, with the C/N of 50 and the pH of 7, and simultaneously performing static culture in an incubator at the temperature of 25 ℃ for 24 hours to serve as a control group. Sampling to determine NH₄ ⁺N, TN content and its pH and OD₆₀₀。

Influence of dissolved oxygen on heterotrophic nitrification performance of LJ9

In general, different bacteria have different sensitivities to dissolved oxygen content. The dissolved oxygen content has obvious influence on nitrification and can even control the nitrification metabolite. Since the dissolved oxygen content is in positive correlation with the rotating speed, the dissolved oxygen content is changed by changing the rotating speed of the shaking table. The results of strain LJ9 affected by different dissolved oxygen contents are shown in FIG. 14: OD of LJ9 at 0rpm, i.e., in stationary culture₆₀₀Only 0.192, the removal of ammonia nitrogen and total nitrogen is only 52.78% and 45.46%, which indicates that the static culture is insufficient in dissolved oxygen and incomplete in nitrification. LJ9 biomass increased with increasing rotational speed, OD at 180rpm₆₀₀Maximum ofThe ammonia nitrogen removal rate is about 94% at the rotation speed of 90-180rpm, the difference is not obvious, the total nitrogen removal rate is 94.08% at the rotation speed of 180rpm, the dissolved oxygen quantity influences the denitrification efficiency of the strain to a certain extent, the biomass, the ammonia nitrogen and the total nitrogen degradation rate are comprehensively considered, and the rotation speed of 180rpm is selected as the subsequent experimental condition.

Aerobic denitrification performance study of pseudomonas LJ9

Inoculating the seed liquid into 200ml aerobic denitrification or nitrosation culture medium triangular conical flask (500 ml) with 3% inoculation amount, wherein the initial nitrate nitrogen concentration or nitrite nitrogen concentration is 100 mg.L^-1The cells were incubated at 30 ℃ and 150rpm for 24 hours with shaking and were sampled every 6 hours for measurement. With NaNO₂Determination of NO in Medium as sole Nitrogen Source₃ ^--N accumulation, pH, NO₂ ^--content of N, TN and COD; with NaNO₃Determination of NO as sole Nitrogen Source₂ ^--N accumulation, pH, NO₃ ^-N, TN and COD content.

Research result of aerobic denitrification performance

The strain LJ9 takes sodium succinate as a carbon source and NaNO₂The growth curve and the nitrosation denitrification curve of 24h of culture are shown in FIG. 15 as the sole nitrogen source: because of the growth lag phase of the thallus, the growth of 0-6h is obviously slower than that of 6-12h, and OD₆₀₀Grow exponentially in 6-12 h. OD at 12h₆₀₀A maximum of 0.347 is reached. OD 12-18h₆₀₀Decline, nutrient deficiency, metabolite accumulation, inhibition of bacterial growth, and increased strain mortality. The time is 18-24h in the stable period. The removal rate of COD tends to be stable within 18-24h, and reaches 87.79% within 24 h. The pH increased with time from 7.37 to finally 7.98.

The nitrosation denitrification process has a small amount of NO₃ ^-Production of-N, 0.394 mg.L in 6h^-1NO of₃ ^-N, which subsequently degrades again, is only 0.163 mg. L for 24h^-1NO of₃ ^-Accumulation of-N, possibly NO if prolonged incubation is used₃ ^--accumulation of N. The strain LJ9 is proved to have aerobic denitrification capability. 24h Strain LJ9 YamThe removal rates of nitrate nitrogen and total nitrogen were 68.89% and 40.62%, respectively. Flavobacterium sp.FL211T pair NO screened by Ganmei et al₂ ^-The denitrification capability of N is low, and the nitrogen removal rate of the sodium nitrite reaches the maximum within 12 hours, but is only about 30 percent. The nitrosation denitrification performance of the strain LJ9 is superior to that of FL 211T.

Strain LJ9 with KNO₃The growth curve for 24h of culture is shown in FIG. 16 as a sole nitrogen source: the growth curve is relatively flat in 0-6h, the strain LJ9 is in a lag phase, the strain LJ9 is in exponential growth in 6-24h, and the OD is₆₀₀From 0.098 to 0.385. Due to the limited nutrient substances, the growth trend of the later strains is obviously slowed down. The removal rate of LJ9COD of the strain reaches 87.92 percent after 24 hours, and the pH value is 8.03. At 18h, the removal rate of the nitrate nitrogen of LJ9 reaches 84.71 percent at the maximum, and the accumulation amount of the nitrite nitrogen reaches the maximum. Nitrite has higher toxicity than nitrate, and due to accumulation of nitrous acid, it has toxic effect on bacterial strain to inhibit denitrification process, and nitrites nitrogen can be nitrified, NO can be obtained at 18-24 hr₃ ^-The N content increases. The removal rate of nitrate nitrogen and total nitrogen by the strain LJ9 is 76.69 percent and 53.30 percent respectively after 24 hours. The actual conversion to nitrogen to remove nitrite nitrogen and nitrate nitrogen was 6.70% and 36.46%, respectively, calculated from the nitrogen balance at 12 h. According to the speculation of the utilization of nitrite nitrogen by LJ9, if the culture time is prolonged, LJ9 can continue to degrade accumulated NO₂ ^--N。

Study on aerobic denitrification of LJ9

1. Influence of C/N on aerobic denitrification and aerobic nitrosation performance of LJ9

Sodium citrate is used as a carbon source, and the concentration of nitrite nitrogen or nitrate nitrogen is 100 mg.L^-1Inoculating the seed liquid into nitrite nitrogen culture medium or nitrate nitrogen culture medium with C/N of 8, 25, 50, 75, 100, 120 at 3%, respectively, culturing at 25 deg.C and 180rpm for 24 hr, sampling, and measuring NO₂ ^--N、NO₃ ^-Content of-N and TN and their pH values and OD₆₀₀。

Influence result of C/N on aerobic denitrification performance of LJ9

Respectively using NaNO as strain LJ9₂And KNO₃Is a unique nitrogen source, and the initial N concentration is 100 mg.L^-1Cultured for 24h, under different C/N, the strain LJ9 is NO₂ ^-The case of-N degradation is shown in FIG. 17: nitrite nitrogen, total nitrogen removal and OD with increasing C/N₆₀₀The pH tended to decrease. OD of Strain LJ9 at C/N8₆₀₀Reaches 0.373, the removal rates of nitrite nitrogen and total nitrogen are the highest, and are respectively 66.6 percent and 60.22 percent; when the C/N is higher than 50, the removal rate of nitrite nitrogen is lower than 20%. The shortage of dissolved oxygen is easily caused by high C/N, and after the requirement of thallus growth metabolism is met, intermediate products generated by excessive carbon sources are accumulated, so that the progress of aerobic nitrosation is inhibited. Meanwhile, nitrite may have toxic effects on the bacteria, so that LJ9 has poor utilization of the nitrite.

Strain LJ9 for NO under different C/N conditions₃ ^-The case of N degradation is shown in FIG. 18: when the C/N is 25-75, the removal rate of nitrate nitrogen reaches more than 99.5%, the removal rate of the total nitrogen is divided into 84.84%, 85.65% and 88.45%, when the C/N is 100, the removal rates of nitrate nitrogen and total nitrogen are slightly reduced to reach 98.68% and 80.01%, respectively, and the total C/N of the LJ9 aerobic denitrification is higher, so that the application range is larger.

Under different C/N conditions, different strains have different denitrification capabilities and a certain application range, and when the C/N reaches a certain value, the aerobic denitrification rate is in a stable state. The strain Bacillus cereus CZ1 easy to separate and study immediately takes potassium nitrate as nitrogen source, most preferably C/N is 6, and when C/N continues to increase, the denitrification efficiency is slightly reduced. The HN-AD bacterium Acinetobacter pitttii A14 screened from Huangting forest, when C/N is 16, NO₃ ^-Complete removal of-N, C/N8 or 20, NO₃ ^-the-N removal rate is reduced. In conclusion, the denitrification efficiency is affected due to insufficient carbon source caused by too low C/N, the denitrification performance of the thalli is easily reduced due to too high C/N, and the optimal C/N for denitrification of the aerobic denitrifying bacteria is 5-8, and less is more than 20. Compared with most aerobic denitrifying bacteria, the strain LJ9 has the capability of tolerating higher C/N, and can provide a new strain resource for treating high C/N organic pollution.

2. Influence of nitrate nitrogen content on aerobic denitrification performance of LJ9

Inoculating the seed solution with sodium citrate as carbon source, C/N of 25, and 3% of inoculum size at nitric acid nitrogen concentrations of 100, 150, 200, 300, 400, and 500 mg.L^-1In the nitrate nitrogen medium, after shaking culture at 25 ℃ and 180rpm for 24 hours, sampling and measuring NO₃ ^-Content of-N and TN and their pH values and OD₆₀₀。

Influence result of nitrate nitrogen content on aerobic denitrification performance of LJ9

Strain LJ9 in different NO₃ ^-Culturing for 24h at-N concentration, NO₃ ^-N removal case is shown in fig. 19: according to the strain LJ9, the biomass, the removal rate of nitrate nitrogen and the pH value are in a negative correlation with the concentration of nitrate nitrogen, namely, as the content of nitrate nitrogen is increased, the removal rate of biomass and nitrate nitrogen is reduced, and the pH value is reduced. When NO is present₃ ^-The concentration of N is 100, 150, 200, 300, 400, 500, 600 mg.L^-1The removal rates of nitrate nitrogen were 99.79%, 98.49%, 95.99%, 96.82%, 95.22%, 92.34%, and 90.05%, respectively, and the removal rates were 4.16, 6.16, 8.00, 12.10, 15.87, 19.24, and 22.51mg (L. h)^-1(ii) a The total nitrogen removal rates were 90.87%, 72.27%, 57.17%, 48.45%, 35.00%, 28.00%, 20.56%, respectively, with corresponding removal rates of 3.79, 4.83, 4.76, 6.06, 5.83, 5.14mg (L.h)^-1. Indicating that the strain LJ9 can tolerate 600 mg.L^-1The nitrate nitrogen concentration of (a) and the nitrate nitrogen removal rate is high, and if the incubation time is prolonged, the total nitrogen removal rate may continue to increase.

The growth and metabolism and denitrification processes of the strain both need enzyme participation, and the excessively high concentration of nitrate nitrogen can influence the substrate concentration of the water environment and is not beneficial to the diffusion of enzymatic reaction; can be combined with an activator of enzyme to reduce the enzymatic reaction rate; meanwhile, excessive substrates are combined with enzyme molecules to form an intermediate product, so that the enzyme is inactivated, and the denitrification efficiency of the strain is inhibited. Different strains have different nitrate nitrogen loading capacities. Acinetobacter sp.HY2 is reported to have initial nitrogen concentrations of 100, 200, 300 mg.L^-1Then, the nitrate nitrogen removal rates for 48h were 85%, 70% and 47%, respectively; pseudomonas putida LY1 at an initial nitrogen concentration of 300 mg.L^-1In time, the nitrate nitrogen removal rate is only 46%; it is likely that higher nitrate nitrogen inhibits the action of denitrification enzymes. And the strain LJ9 can tolerate the nitrate nitrogen concentration as high as 600 mg.L^-1And the nitrate nitrogen removal rate can reach 90.05% in 24h, which shows that the influence of nitrate inhibition on the LJ9 aerobic denitrification reaction process is small, and the aerobic denitrification performance of the strain is superior to that of most aerobic denitrification strains reported at present.

3. Influence of nitrite nitrogen content on aerobic nitrosation performance of LJ9

Inoculating seed solution with 3% inoculum size of sodium citrate as carbon source and C/N of 8 into nitrous acid solution with nitrogen concentration of 100, 150, 200, 300, 400, 500 mg.L^-1In the nitrite nitrogen culture medium, after shaking culture at 25 ℃ and 180rpm for 24 hours, sampling and measuring NO₂ ^-Content of-N and TN and their pH values and OD₆₀₀。

Influence result of nitrite nitrogen content on LJ9 aerobic nitrosation performance

Strain LJ9 in different NO₂ ^-Culturing for 24h at-N concentration, NO₂ ^-The removal of-N is shown in fig. 20: OD as nitrite nitrogen concentration increases₆₀₀Gradually decreases. When initial NO₂ ^-N concentration of 100 mg.L^-1And 150 mg. L^-1The bacterial strain LJ9 has high removal rate of nitrite nitrogen and total nitrogen, which is 54.64%, 45.84%, 48.46% and 44.60% respectively; initial nitrite nitrogen concentration of 200 mg.L^-1The removal rate of nitrite nitrogen is low; initial N concentration of 300 mg.L^-1When present, nitrite nitrogen is not degraded. Nitrite nitrogen concentrations of 100, 150, 200, 300 mg.L respectively^-1The removal rates of nitrite nitrogen are 2.28, 2.87, 1.28 and 0.00mg (L.h)^-1The total nitrogen removal rates are 2.02, 2.79, 0.44, 0.02mg (L.h)^-1。

Different kinds of bacteria have different tolerance degrees on nitrite nitrogen, and when the concentration of the nitrite is too low, the requirement for the growth of the bacteria cannot be metThe nitrogen source with too high concentration can produce toxic action on the microorganism and inhibit denitrification. For example: initial nitrite nitrogen concentration of 10 mg.L of Pseudomonas talasiY-11^-1And 48h, the removal rates of nitrite nitrogen and total nitrogen respectively reach 100% and 63.1%, and the removal rate of nitrite nitrogen is reduced along with the increase of concentration. Bacillus coaguluns YX-6 with initial nitrite nitrogen concentration of 20 mg.L^-1When the concentration of the nitrite nitrogen is increased to 100 mg.L, the removal rate of the nitrite nitrogen is close to 100 percent^-1The removal rate of nitrite nitrogen is only 20%. Compared with the strain, the strain LJ9 can tolerate nitrite nitrogen with higher concentration, can more effectively solve the problem of nitrite accumulation, is not easy to be inhibited by nitrite in the aerobic denitrification reaction process, and can provide a strain source for high nitrite nitrogen wastewater treatment.

The above description is only for the preferred embodiment of the present application and should not be taken as limiting the present application in any way, and although the present application has been disclosed in the preferred embodiment, it is not intended to limit the present application, and those skilled in the art should understand that they can make various changes and modifications within the technical scope of the present application without departing from the scope of the present application, and therefore all the changes and modifications can be made within the technical scope of the present application.

Claims

1. A method for treating ammonia nitrogen wastewater by using heterotrophic nitrification-aerobic denitrification pseudomonas strains is characterized in that the ammonia nitrogen wastewater contains organic acid sodium, the C/N ratio of the ammonia nitrogen wastewater is 8-120, and the method comprises the following steps:

2. root of herbaceous plantThe method for treating ammonia nitrogen wastewater by using the pseudomonas strain for heterotrophic nitrification-aerobic denitrification as claimed in claim 1, wherein the concentration of ammonia nitrogen in the ammonia nitrogen wastewater is 100 mg-L^-1～500mg·L^-1。

3. The method for treating ammonia nitrogen wastewater by using the pseudomonas strain subjected to heterotrophic nitrification-aerobic denitrification as claimed in claim 2, wherein the C/N ratio of the ammonia nitrogen wastewater is 8-100, and the concentration of the ammonia nitrogen is 100 mg-L^-1～400mg·L^-1。

4. The method for treating ammonia nitrogen wastewater by using the pseudomonas strain subjected to heterotrophic nitrification-aerobic denitrification as claimed in claim 3, wherein the inoculation amount of the pseudomonas seed solution subjected to heterotrophic nitrification-aerobic denitrification is 3% -5%.

5. The method for treating ammonia nitrogen wastewater by using the pseudomonas strain subjected to heterotrophic nitrification-aerobic denitrification as claimed in claim 4, wherein the pH value of the ammonia nitrogen wastewater is 6-9.

6. The method for treating ammonia nitrogen wastewater by using the pseudomonas strain subjected to heterotrophic nitrification-aerobic denitrification as claimed in claim 5, wherein the sodium organic acid is one or more of sodium citrate, sodium succinate and sodium acetate.

7. The method for treating ammonia nitrogen wastewater by using the heterotrophic nitrification-aerobic denitrification pseudomonas strain as claimed in any one of claims 1 to 6, wherein the heterotrophic nitrification-aerobic denitrification pseudomonas seed solution is prepared by the following method:

8. The method for treating ammonia nitrogen wastewater by using the pseudomonas strain subjected to heterotrophic nitrification-aerobic denitrification as claimed in claim 7, wherein the culture process comprises the following steps: performing shaking culture at 25-35 ℃ and 100-180 rpm for 12-18 h.

9. The method for treating ammonia nitrogen wastewater by using the pseudomonas strain subjected to heterotrophic nitrification-aerobic denitrification as claimed in claim 7, wherein the LB medium comprises the following components: bacteriological peptone 10 g.L^-15 g.L yeast extract^-1，NaCl 10g·L^-1，pH 7.0。

10. The method for treating ammonia nitrogen wastewater by using the pseudomonas strain subjected to heterotrophic nitrification-aerobic denitrification as claimed in claim 7, wherein sterile water is added to the bacterial liquid OD₆₀₀0.6 to 0.8.