JP2006289347A - Method and apparatus for treating waste water - Google Patents

Abstract

<P>PROBLEM TO BE SOLVED: To provide a method and apparatus for treating waste water capable of shortening the start-up period for the apparatus and of high-speed, stable denitrification during normal operation after the start-up period which cannot be achieved by conventional anaerobic ammonia oxidizing bacteria. <P>SOLUTION: In the treatment of the waste water containing nitrogen, at least ammonia, in an anaerobic ammonia oxidizing bath 18 using the anaerobic ammonia oxidizing bacteria for denitrification with ammonia and nitrous acid as a substrate, the collected sludge in which the anaerobic ammonia oxidizing bacteria having a specific proliferation rate of 0.39 per day or more in seed sludge are collected and cultured is brought into contact with the waste water containing nitrogen in the anaerobic ammonia oxidizing bath 18. <P>COPYRIGHT: (C)2007,JPO&INPIT

Description

  The present invention relates to a wastewater treatment method and apparatus, and more particularly, to a wastewater treatment method and apparatus using anaerobic ammonia-oxidizing bacteria that are used for nitrogen removal of nitrogen-containing wastewater containing at least ammonia and using ammonia and nitrous acid as substrates. .

  In food factories and chemical factories, various concentrations of ammonia from low to high concentrations are discharged as waste water. These ammonia waste liquids cause eutrophication of water bodies and decrease in dissolved oxygen, and the necessity for treatment is strongly desired.

  In general, in the treatment of ammonia waste liquid from low concentration to medium concentration, many biological biological treatments using microorganisms are performed. In this biological treatment, nitrification / denitrification treatment by aerobic nitrification and anaerobic denitrification is performed. Aerobic nitrification is treated in the nitrification tank with ammonia oxidizing bacteria (genus Nitrosomonas, Nitrosococcus, Nitrosospira, Nitrosolobus, etc.) and nitrite oxidizing bacteria (Nitrobactor, Nitrospira, Nitrococcus, Nitospina, etc.). Aerobic oxidation of ammonia nitrogen and nitrite nitrogen in the nitrogen-containing wastewater. On the other hand, anaerobic denitrification involves anaerobic denitrification by heterotrophic bacteria such as Pseudomonas denitrificans in a denitrification tank.

In aerobic nitrification, the nitrification tank is operated at a load of 0.2 to 0.3 kg-N / m ³ / day. On the other hand, in anaerobic denitrification, the denitrification tank is operated at a load of 0.2 to 0.4 kg-N / m ³ / day. Therefore, when the total nitrogen concentration in the nitrogen-containing wastewater to be treated is in the range of 30 to 40 mg / L, a residence time of 6 to 8 hours is required in the nitrification tank and 5 to 8 hours in the denitrification tank. There was a problem that a large-scale wastewater treatment device had to be provided.

  In addition, in nitrogen-containing wastewater containing only inorganic substances such as industrial wastewater, the loads of the nitrification tank and the denitrification tank are set in the same manner as described above, but organic matter is required when performing denitrification. Therefore, it is necessary to add methanol having a concentration of 3 to 4 times the nitrogen concentration in the nitrogen-containing wastewater to be treated, and there is a new problem that not only the initial cost but also a great running cost is required.

  On the other hand, recently, as disclosed in Patent Document 1, attention has been paid to nitrogen removal by an anaerobic ammonia oxidation method in which the following reaction is performed. In this method, a part of ammonia is converted into nitrite by a nitrite type nitrifying bacterium, and this nitrite and the remaining ammonia are simultaneously denitrified by an anaerobic ammonia oxidizing bacterium. This method has the merit that the processing cost is low because a part of ammonia is converted into nitrous acid, so that the amount of necessary oxygen is small and denitrification can be performed with an organic substance.

[Chemical 1]
NH ₄ + + 1.32NO ₂ + 0.066HCO ₃ + 0.13H ⁺
→ 1.02N ₂ + 0.26NO ₃ + 0.066CH ₂ O _0.5 N _0.15 + 2.03H ₂ O
JP 2001-037467 A

  However, it has been reported that anaerobic ammonia-oxidizing bacteria require 11 days as the time required for one cell to grow into two cells (doubling time), and the growth rate is slow and the cell yield is low. In addition, it takes time to start up a wastewater treatment apparatus using an anaerobic ammonia oxidation method, and it is difficult to retain a high concentration of anaerobic ammonia oxidation bacteria in a treatment tank, and thus there is a problem that stable wastewater treatment cannot be performed.

  The present invention has been made in view of such circumstances, and the startup period of the apparatus can be shortened, and stable high-speed denitrification that cannot be obtained by conventional anaerobic ammonia-oxidizing bacteria during steady operation after startup. It is an object of the present invention to provide a wastewater treatment method and apparatus that can be performed and that can greatly reduce the size of the apparatus compared to conventional nitrification / denitrification methods.

In order to achieve the above object, claim 1 of the present invention is a wastewater treatment in which nitrogen-containing wastewater containing at least ammonia is treated in a treatment tank using anaerobic ammonia-oxidizing bacteria that perform denitrification using nitrous acid and ammonia as substrates. In the method, in the treatment tank, the wastewater treatment method is characterized in that the accumulated sludge in which the anaerobic ammonia-oxidizing bacteria having a specific growth rate of 0.39 day- ¹ or more from the seed sludge is brought into contact with the nitrogen-containing wastewater. I will provide a.

  Here, the nitrogen-containing wastewater is nitrogen-containing wastewater containing at least ammonia, and nitrous acid, which is another substrate of anaerobic ammonia-oxidizing bacteria, can be obtained by various methods. For example, even if it is contained in nitrogen-containing wastewater, a part of ammonia contained in the nitrogen-containing wastewater may be nitrified with nitrifying bacteria to generate nitrous acid, or added from a tank or the like to the treatment tank. May be. Furthermore, ammonia may be nitrified with nitrifying bacteria to form nitric acid, and this nitric acid may be bioreduced to produce nitrous acid. Moreover, as seed sludge, activated sludge and digested sludge can be used conveniently, for example.

The present inventor has found that among the types of anaerobic ammonia oxidizing bacteria, there are anaerobic ammonia oxidizing bacteria having a very fast growth rate having a specific growth rate of 0.39 day ^-1 or more. A technology for enrichment culture of fast anaerobic ammonia oxidizing bacteria was established. And it was found that the anaerobic ammonia-oxidizing bacteria that were cultivated in an integrated manner could be treated stably by holding the accumulated sludge in the treatment tank.

According to claim 1, when treating nitrogen-containing treated water using anaerobic ammonia oxidizing bacteria, anaerobic ammonia oxidizing as anaerobic ammonia oxidizing bacteria having a specific growth rate of 0.39 day- ¹ or more from seed sludge. Since the anaerobic ammonia-oxidizing bacteria and nitrogen-containing wastewater are brought into contact with each other using bacteria accumulated in culture, the start-up period of the apparatus can be shortened, and the conventional anaerobic operation is possible during steady operation after start-up. High-speed denitrification that cannot be obtained with ammonia-oxidizing bacteria can be performed stably.

A second aspect of the present invention is the first aspect of the present invention, wherein the accumulated sludge is obtained by holding the seed sludge in a culture tank and passing a culture solution containing at least the substrate at a dilution rate of 0.39 to 24 days- ¹ . It is characterized by being concentrated and cultured.

Claim 2 is a method for accumulating and accumulating accumulated sludge containing anaerobic ammonia-oxidizing bacteria having a specific growth rate of 0.39 day ^-1 or more. The seed sludge is retained in the culture tank, and the dilution rate is 0.39. The culture solution was allowed to flow through -24 days ^-1 . As a result, bacteria other than the anaerobic ammonia-oxidizing bacteria in the present invention having a specific growth rate of 0.39 day ^-1 or more are washed out (washed out from the culture tank), and accumulated in the accumulated sludge obtained by the accumulation culture. Has a high concentration of anaerobic ammonia-oxidizing bacteria with a specific growth rate of 0.39 day- ¹ or more. By using this accumulated sludge for wastewater treatment, stable high-speed denitrification treatment can be performed. A more preferable condition for the dilution rate (day- ¹ ) is 1-8 days- ¹ .

A third aspect is characterized in that, in the first or second aspect, the accumulated sludge contains 10 ⁵ cells / mL or more of the anaerobic ammonia oxidizing bacteria.

This is because, in order to obtain a high denitrification rate in the treatment tank, it is preferable that the accumulated sludge contains anaerobic ammonia-oxidizing bacteria at a concentration of 10 5 cells / mL or more. More preferably, 10 ⁶ cells / mL or more is contained in the accumulated sludge, and 10 ⁷ cells / mL or more is particularly preferred.

  A fourth aspect of the present invention is characterized in that, in any one of the first to third aspects, the accumulated sludge is held in any form of an adhesion immobilization carrier, a entrapping immobilization carrier, and a self-granulated product.

  In this way, if the accumulated sludge is held in any form of an adhesion immobilization carrier, a entrapping immobilization carrier, or a self-granulated product, anaerobic ammonia-oxidizing bacteria are less likely to flow out of the treatment tank. The anaerobic ammonia oxidizing bacteria concentration can be maintained at a high concentration.

  5. The C / N ratio, which is a ratio of the amount of organic carbon C and the total amount of nitrogen N in the nitrogen-containing treated water, is 0.1 or more and 3 or less. And

  This is because a high nitrogen removal rate can be obtained when the C / N ratio is 0.1 or more and 3 or less, and a more preferable range is 0.2 to 1.

  6. The method according to any one of claims 1 to 5, wherein the treatment tank is treated under anaerobic conditions.

  Anaerobic ammonia-oxidizing bacteria are anaerobic bacteria, and the atmosphere in the treatment tank is formed accordingly.

  7. The process according to claim 1, wherein the treatment tank is filled with the entrapped immobilization support for the anaerobic ammonia-oxidizing bacteria and the nitrified sludge containing the nitrifying bacteria. The treatment is performed under tempering conditions.

  The anaerobic ammonia oxidizing bacterium is an anaerobic bacterium. However, when the entrapping immobilization support and the nitrified sludge of the anaerobic ammonia oxidizing bacterium are put into the treatment tank as in claim 7, the anaerobic ammonia oxidizing bacterium is placed outside the entrapping immobilization support. Since a biofilm of nitrified sludge is formed, an attached / entrapped carrier in which nitrifying bacteria that are aerobic bacteria exist outside and anaerobic ammonia oxidizing bacteria that are anaerobic bacteria exist inside is formed. And if the inside of a processing tank is made into an aerobic condition and it processes using an adhesion | attachment and a comprehensive support | carrier, nitrification reaction and anaerobic ammonia oxidation reaction can be performed with one processing tank.

  In order to achieve the above object, claim 8 of the present invention is a wastewater treatment for treating nitrogen-containing wastewater containing at least ammonia in a treatment tank by using anaerobic ammonia oxidizing bacteria that perform denitrification using nitrous acid and ammonia as substrates. In the apparatus, a wastewater treatment apparatus is provided, wherein the treatment tank is filled with an accumulated sludge obtained by accumulating anaerobic ammonia-oxidizing bacteria having a specific growth rate of 0.39 day-1 or more from the seed sludge. To do.

  Claim 8 comprises the present invention as an apparatus, which can shorten the start-up period of the apparatus and stabilize high-speed denitrification that cannot be obtained by conventional anaerobic ammonia-oxidizing bacteria during steady operation after start-up. Can be done. In addition, it can be made much more compact than conventional nitrification / denitrification equipment.

  A ninth aspect of the present invention according to the eighth aspect is characterized in that the wastewater treatment apparatus is provided with a nitrification tank for converting a part of ammonia in the nitrogen-containing wastewater into nitrous acid and / or nitric acid.

  Claim 9 is one embodiment for obtaining nitrous acid among ammonia and nitrous acid, which is a substrate of anaerobic ammonia oxidizing bacteria, and in the nitrification tank, a part of ammonia in the nitrogen-containing wastewater is converted to nitrous acid and / or This is converted to nitric acid.

  In this case, conversion from ammonia to nitrite can be achieved by a nitrite type nitrification tank mainly composed of ammonia oxidizing bacteria. In addition, in order to obtain nitrite from ammonia via nitric acid, in addition to a normal nitrification tank containing ammonia-oxidizing bacteria and nitrite-oxidizing bacteria, a denitrification tank containing heterotrophic denitrifying bacteria and organic matter is used. Can be achieved. That is, ammonia is nitrified to ammonia by ammonia-oxidizing bacteria and nitrite-oxidizing bacteria, and the resulting nitric acid is bioreduced to nitrous acid by heterotrophic denitrifying bacteria using organic substances as hydrogen donors.

  A tenth aspect of the present invention is characterized in that, in the eighth or ninth aspect, the wastewater treatment apparatus is provided with a heterotrophic denitrification tank that reduces nitric acid to nitrous acid.

  A tenth aspect is provided with a denitrification tank for obtaining nitrous acid from the nitric acid described in the tenth aspect, wherein nitric acid is reduced to nitrous acid by a heterotrophic denitrification tank. This reduction from nitric acid to nitrous acid requires an organic substance as a hydrogen donor, and is therefore suitable when there is too much organic substance contained in the nitrogen-containing wastewater.

  An eleventh aspect of the present invention is the wastewater treatment apparatus according to any one of the eighth to tenth aspects, wherein the wastewater treatment apparatus is provided with an organic substance addition means for adding an organic substance into the treatment tank.

  Claim 11 is suitable when the amount of organic matter contained in the nitrogen-containing wastewater is too small.

  A twelfth aspect is characterized in that, in any one of the eighth to eleventh aspects, the treatment is performed in an anaerobic condition in the treatment tank.

  Anaerobic ammonia-oxidizing bacteria are anaerobic bacteria, and the atmosphere in the treatment tank is formed accordingly.

  A thirteenth aspect of the present invention is the method according to any one of the eighth to eleventh aspects, wherein the entrapped immobilization support for the anaerobic ammonia-oxidizing bacteria and nitrified sludge are introduced into the treatment tank, and air is aerated in the treatment tank. An air aeration means is provided.

  The thirteenth aspect constitutes the seventh aspect as an apparatus.

  As described above, according to the wastewater treatment method and apparatus according to the present invention, the startup period of the apparatus can be shortened, and high-speed denitrification that cannot be obtained by conventional anaerobic ammonia-oxidizing bacteria during steady operation after startup. Can be performed stably. In addition, the apparatus can be made more compact than the conventional nitrification / denitrification method.

  Hereinafter, preferred embodiments of an anaerobic ammonia-oxidizing bacteria culture method and apparatus according to the present invention will be described in detail with reference to the accompanying drawings.

The present inventor has found that among anaerobic ammonia-oxidizing bacteria, there are cells with a very high growth rate having a specific growth rate of 0.39 day- ¹ or more. A technique for enrichment culture was established. Then, by establishing a preferable concentration of bacteria in the accumulated sludge when using the accumulated sludge accumulated and cultured, and a preferable method for retaining the accumulated sludge, a waste water treatment device is specifically configured as an actual device, thereby anaerobic ammonia. The start-up period by the oxidation method is shortened, and stable high-speed denitrification during steady operation is achieved.

[A] First, an anaerobic ammonia oxidizing bacterium having a specific growth rate of 0.39 day- ¹ or more found in the present invention will be described.

The anaerobic ammonia oxidizing bacterium having a specific growth rate of 0.39 day- ¹ or more is the one in which the specific region of the DNA base sequence based on the 16S rRNA gene is shown in SEQ ID NOs: 1 to 9 in the sequence listing shown at the end of the specification. Including at least one of the following.

  The specific growth rate of anaerobic ammonia-oxidizing bacteria having the above gene sequence was determined by measuring by the FISH method. The FISH method uses a probe that develops color only for the genes of anaerobic ammonia-oxidizing bacteria. The sample is dispersed with ultrasound, then stained with an AMX820 probe, and counted directly under a trend microscope. The number of bacteria was calculated.

  The nine gene sequences in the present invention were registered with DDBJ (DNA Data Bank of Japan). The registration number of SEQ ID NO: 1 is AB164467, the registration number of SEQ ID NO: 2 is AB164468, the registration number of SEQ ID NO: 3 is AB164469, the registration number of SEQ ID NO: 4 is AB164470, the registration number of SEQ ID NO: 5 is AB164471, the registration of SEQ ID NO: 6 The registration number of sequence number 7 is AB164473, the registration number of sequence number 8 is AB164474, and the registration number of sequence number 9 is AB164475.

[B] Next, a culture method for accumulating anaerobic ammonia-oxidizing bacteria having a specific growth rate of 0.39 day- ¹ or more will be described.

In the culture test, seed sludge containing anaerobic ammonia-oxidizing bacteria having a specific growth rate of 0.39 day- ¹ or more is retained in the culture tank, and contains at least ammonia and nitrous acid, which are substrates for anaerobic ammonia-oxidizing bacteria. The culture solution (for example, Table 1) to be passed through was continuously cultured. The dilution rate (day- ¹ ) in continuous culture was between 0.1 and 100. The dilution rate is defined by the following formula used in continuous culture, dX / dt = μ · X−D · X.

図１は、培養試験の結果であり、比増殖速度が０．３９日^-1以上の嫌気性アンモニア酸化細菌の菌数（cells/mL）と希釈率（日^-1）との関係、及び共存する細菌と希釈率（日^-1）との関係を示したものである。 Here, μ: specific growth rate, X: bacterial cell concentration (cells / mL), t: culture time (day), D: dilution rate (day −1).

Fig. 1 shows the results of the culture test. The relationship between the number of anaerobic ammonia-oxidizing bacteria (cells / mL) and dilution rate (day- ¹ ) with a specific growth rate of 0.39 day- ¹ or more, and coexistence This shows the relationship between the bacteria to be used and the dilution rate (day- ¹ ).

In FIG. 1, the “anaerobic ammonia oxidizing bacterium of the present invention” is an anaerobic ammonia oxidizing bacterium having a specific growth rate of 0.39 day ⁻¹ or more, and the “coexisting bacteria” is “anaerobic ammonia of the present invention”. Bacteria other than “oxidizing bacteria”.

As shown in FIG. 1, as the dilution rate is increased, the number of anaerobic ammonia-oxidizing bacteria having a rapid growth rate with a specific growth rate of 0.39 day ⁻¹ or more increases rapidly. 1 (day ^-1) number of bacteria when it is intended was 10 ³ (cells / mL), the dilution factor 0.39 (day ^-1) 10 bacteria count twice in ⁶ (cells / mL) Become. Further increasing the dilution rate, the peak at a dilution 1 (day ^-1) number of bacteria becomes 10 ⁸ (cells / mL), the number of bacteria at a dilution 3 (day ^-1) 10 ⁹ (cells / mL) To reach. The number of bacteria remained at 10 ⁹ (cells / mL) up to a dilution rate of 8 (day ^-1 ), and then the number of bacteria gradually decreased to nearly 10 ⁶ (cells / mL) at a dilution rate of 24 (day ^-1 ). To fall.

In contrast, the coexisting bacteria had a dilution rate of 1 (day- ¹ ) and the number of bacteria was high between 10 ⁸ (cells / mL) and 10 ⁹ (cells / mL). As the value is increased, the number of bacteria rapidly decreases and decreases to near 10 ³ (cells / mL) at a dilution rate of 24 (day ⁻¹ ).

As described above, when the enrichment culture is performed at a dilution rate larger than the dilution rate 0.1 set in the normal enrichment culture, the anaerobic ammonia oxidation having a rapid growth rate of a specific growth rate of 0.39 day- ¹ or more. It can be seen that bacteria are accumulated and other coexisting bacteria are washed out of the culture tank because the dilution rate is too large. As a result, anaerobic ammonia-oxidizing bacteria having a specific growth rate of 0.39 day- ¹ or more are accumulated in the accumulated sludge at a high concentration.

In order to perform stable high-speed denitrification in a wastewater treatment apparatus, it is preferable that the number of bacteria in the accumulated sludge is at least 10 ⁵ (cells / mL) or more, as can be seen from [C] described later. Moreover, it is preferable that the anaerobic ammonia oxidizing bacteria is about half or more of the coexisting bacteria. This result, as a method of enrichment culture specific growth rate to zero. Day 39 ^-1 or more growth rate fast anaerobic ammonium oxidizing bacteria, to liquid permeation of the culture solution at a dilution from 0.39 to 24 days ^-1 The dilution ratio is more preferably ¹ to 10 days ⁻¹ , and the dilution ratio 3 to 8 days ⁻¹ is particularly preferable.

Actually, activated sludge from an sewage treatment plant or anaerobic digested sludge is used as seed sludge, ammonia nitrogen concentration, nitrite nitrogen concentration, nitrate nitrogen concentration is 1: 1: 3, and total nitrogen concentration is 80 mg / L. 10 ⁶ (cells / mL) of anaerobic ammonia-oxidizing bacteria having a specific growth rate of 0.39 day ^{- 1} or more in about 5 months. It was possible to cultivate the cells so that the number of bacteria would be as high as possible. When the dilution rate is 3 to 8 (day- ¹ ), anaerobic ammonia-oxidizing bacteria with a specific growth rate of 0.39 day- ¹ or higher should be cultured at a high concentration up to 10 ⁸ (cells / mL). I was able to.

As can be seen from this result, the dilution rate (day ^-1 ) is important under conditions where there is sufficient nitrogen substrate, and it is accumulated so that it is not affected by the substrate concentration by setting the dilution rate (day ^-1 ) appropriately. It can be cultured. As the total nitrogen concentration of the culture solution, a range of 30 to 400 mg / L can be preferably used, but a range of 30 to 100 mg / L is more preferable.
[C] Next, the relationship between the number of anaerobic ammonia-oxidizing bacteria in the accumulated sludge accumulated and cultured as described above and the denitrification rate will be described.

FIG. 2 shows the relationship between the number of anaerobic ammonia-oxidizing bacteria of the present invention having a specific growth rate of 0.39 day ⁻¹ or more and the denitrification rate, and the ammonia concentration in the wastewater is 20 mg / L. Three test sections (low concentration), 70 mg / L (medium concentration), and 200 mg / L (high concentration) were tested. Nitrous acid, another substrate for anaerobic ammonia-oxidizing bacteria, was added from the tank so that the nitrogen concentration was 1.32 times the nitrogen concentration of ammonia in the wastewater.

As can be seen from the graph of FIG. 2, although there are some differences between the three test plots, a denitrification rate of 0.3 (by an amount of 10 ⁵ (cells / mL) or more of the anaerobic ammonia oxidizing bacteria in the accumulated sludge is maintained. kg-N / m ³ / day), and high-speed denitrification is possible. In particular, when the number of bacteria is 10 ⁷ (cells / mL) or more, even a high concentration ammonia wastewater has a denitrification rate of 0.8 (kg-N / m ³ / day) or more, which is a conventional anaerobic ammonia oxidizing bacterium. High-speed denitrification that could not be obtained is possible.
[D] Next, a method for retaining anaerobic ammonia-oxidizing bacteria accumulated and cultured as described above will be described.

  As a method for retaining anaerobic ammonia-oxidizing bacteria, two methods of adhesion immobilization and entrapping immobilization generally known as immobilization of bacteria can be preferably used. Granules may be used.

  The adhesion immobilization method is a method of adhering and holding anaerobic ammonia oxidizing bacteria on the surface of the adhesion immobilization material, and has a large surface area such as a spherical carrier, a cylindrical carrier, a string carrier, a gel carrier, and a nonwoven material. When an adhesion immobilization material with many irregularities is used on the surface, a large amount of anaerobic ammonia-oxidizing bacteria can be retained, and the processing performance is improved.

  The entrapping immobilization method mixes anaerobic ammonia-oxidizing bacteria (accumulated sludge) and entrapping immobilization materials (monomer, prepolymer) and polymerizes the mixture to retain the anaerobic ammonia-oxidizing bacteria inside the gel carrier. Is the method. As the monomer material, acrylamide, methylenebisacrylamide, triacryl formal and the like can be suitably used. As the prepolymer, polyethylene glycol diacrylate or polyethylene glycol methacrylate can be suitably used. The shape of the entrapping immobilization carrier has a shape with a large surface area and a lot of irregularities on the surface, such as a spherical or cylindrical entrapping immobilization carrier, a string-like entrapping immobilization carrier, a non-woven wrapping immobilization carrier, etc. Processing performance is improved.

  Table 2 shows typical composition examples of the entrapping immobilization carrier.

表２の組成の懸濁液に過硫酸カリウムを０．２５部添加すると重合が始まり、ゲル化する。このゲルを切断し、任意の大きさにすることにより、比増殖速度が０．３９日^-1以上の嫌気性アンモニア酸化細菌を高濃度に含有する包括固定化担体を製造することができる。
［Ｅ］次に、比増殖速度が０．３９日^-1以上の嫌気性アンモニア酸化細菌の活性を効果的に発現させる有機物の必要性について説明する。

When 0.25 part of potassium persulfate is added to the suspension having the composition shown in Table 2, polymerization starts and gelation occurs. By cutting this gel and making it an arbitrary size, it is possible to produce a entrapping immobilization carrier containing anaerobic ammonia-oxidizing bacteria having a specific growth rate of 0.39 day ^-1 or more in a high concentration.
[E] Next, the necessity of an organic substance that effectively expresses the activity of anaerobic ammonia-oxidizing bacteria having a specific growth rate of 0.39 day- ¹ or more will be described.

  The test was conducted to examine how the total nitrogen removal rate changes when the C / N ratio in the treatment tank for treating nitrogen-containing wastewater is changed using the accumulated sludge accumulated and cultured as described above. As nitrogen-containing wastewater, the ratio of ammonia nitrogen concentration, nitrite nitrogen concentration, nitrate nitrogen concentration is 1: 0.5: 0.5, and the total nitrogen concentration (TN concentration) is 80 mg / L. Inorganic synthetic wastewater was used. In addition, using sodium acetate as the organic carbon source and changing the C / N ratio by changing the amount of sodium acetate added, a batch test was conducted to examine the total nitrogen removal rate in the stable period 4 hours after the start of operation. It was.

  FIG. 3 is a test result showing the relationship between the C / N ratio, which is the ratio between the amount of organic carbon C and the total nitrogen N in the treatment tank, and the total nitrogen removal rate (TN removal rate) of nitrogen-containing wastewater. is there. As can be seen from FIG. 3, as the C / N ratio is increased, the total nitrogen removal rate increases rapidly, the C / N ratio is 0.1, and the total nitrogen removal rate is 40%. A ratio of 0.2 results in a total nitrogen removal rate of 80%. After the C / N ratio is 0.5 and the total nitrogen removal rate reaches a peak at about 90%, and the peak state is maintained up to about C / N ratio of about 0.8, the total nitrogen removal rate gradually decreases. When the / N ratio is 3, the total nitrogen removal rate is about 60%.

From this result, in order to obtain a high total nitrogen removal rate, it is preferable that the C / N ratio is 0.1 or more and 3 or less, and a more preferable C / N ratio is in the range of 0.2 to 1.
[F] Next, a specific configuration of the wastewater treatment apparatus of the present invention using anaerobic ammonia oxidizing bacteria having a specific growth rate of 0.39 day- ¹ or more will be described below.
(F-1) FIG. 4 shows the wastewater treatment apparatus 10 according to the first embodiment of the present invention, in which part of the nitrogen-containing wastewater containing at least ammonia flows into the branch pipe 14 branched from the raw water pipe 12. While flowing into the nitrification tank 16 from the path 14A, the remaining nitrogen-containing wastewater flows through the raw water pipe 12 and flows into the anaerobic ammonia oxidation tank (corresponding to the treatment tank) 18. The nitrifying bacteria that live in the nitrification tank 16 include ammonia oxidizing bacteria that convert ammonia into nitrite and nitrite oxidizing bacteria that convert nitrite into nitric acid. Thereby, ammonia in nitrogen-containing wastewater is converted into nitrous acid and / or nitric acid. Any holding form of the nitrifying bacteria in the nitrifying tank 16 may be used. For example, adhesion fixing or entrapping fixing is preferably used. On the other hand, in the anaerobic ammonia oxidation tank 18, accumulated sludge in which anaerobic ammonia oxidizing bacteria having a specific growth rate of 0.39 day ⁻¹ or more is accumulated and inhabited is inhabited. The anaerobic ammonia oxidizing bacteria may be inhabited as floating sludge, but is preferably held in the anaerobic ammonia oxidizing tank 18 by adhesion fixation, comprehensive fixation, self-granulation or the like. In FIG. 4, an example of the entrapping immobilization carrier 20 is shown. A screen 22 for preventing the entrapping immobilization carrier 20 from flowing out is provided at the treated water outflow portion of the anaerobic ammonia oxidation tank 18.

  Then, the nitrification liquid containing nitrous acid and / or nitric acid generated in the nitrification tank 16 is supplied from the outflow path 14B of the branch pipe 14 to the anaerobic ammonia oxidation tank 18. As a result, in the anaerobic ammonia oxidation tank 18, anaerobic ammonia oxidation reaction is performed using ammonia flowing from the raw water pipe 12 and nitrous acid flowing from the nitrification tank 16 as substrates, thereby simultaneously denitrifying ammonia and nitrous acid. . Here, the nitric acid supplied from the nitrification tank 16 to the anaerobic ammonia oxidation tank 18 is denitrified (bioreduced) by heterotrophic denitrifying bacteria using the organic matter in the anaerobic ammonia oxidation tank 18 as a hydrogen donor, After being converted to nitric acid, it is used as a substrate.

  The treated water treated in the anaerobic ammonia oxidation tank 18 is discharged out of the system from the treated water pipe 24. Thereby, nitrogen in nitrogen-containing wastewater is removed. The ratio of ammonia and nitrous acid in the anaerobic ammonia oxidation tank 18 is preferably in the vicinity of 1: 1.32. The same applies hereinafter.

  In this wastewater treatment apparatus 10, the start-up period of the apparatus is established by inhaling accumulated sludge in which anaerobic ammonia-oxidizing bacteria having a specific growth rate of 0.39 day -1 or more are accumulated and cultured in the anaerobic ammonia oxidation tank 18. And high-speed denitrification can be stably performed during the steady operation of the apparatus.

In another embodiment of the waste water treatment apparatus described below, the holding forms of the ammonia-oxidizing bacteria and the anaerobic ammonia-oxidizing bacteria living in the nitrification tank 14 and the anaerobic ammonia-oxidizing tank 18 are the same and are omitted. Further, the description of the screen and the treated water piping is also omitted.
(F-2) FIG. 5 shows the wastewater treatment apparatus 30 according to the second embodiment of the present invention, in which the nitrification reaction and the anaerobic ammonia oxidation reaction are performed in one tank of the anaerobic ammonia oxidation tank 18.

The nitrogen-containing wastewater containing at least ammonia flows into the anaerobic ammonia oxidation tank 18 provided with the air aeration pipe 26 from the raw water pipe 12. In the anaerobic ammonia oxidation tank 18, a entrapped immobilization carrier in which the accumulated sludge obtained by culturing anaerobic ammonia oxidizing bacteria is entrapped and a nitrifying sludge containing nitrifying bacteria are introduced. As a result, nitrified sludge adheres to the surface of the entrapping immobilization support, so that a biofilm layer of nitrifying bacteria that are aerobic bacteria is formed outside the aerobic state, and anaerobic ammonia-oxidizing bacteria are formed inside the anaerobic state. The adhesion / entrapping carrier 28 inclusively fixed is formed. Then, the ammonia in the nitrogen-containing wastewater that has flowed into the anaerobic ammonia oxidation tank 18 comes into contact with the nitrifying bacteria of the adhesion / entrapping carrier 28 in an aerobic state, and a part of the ammonia is nitrified to produce nitrous acid. The generated nitrous acid and the remaining ammonia react in an anaerobic state with the anaerobic ammonia-oxidizing bacteria of the adhesion / entrapping carrier 28, and ammonia and nitrous acid are simultaneously denitrified. In this case, it is preferable that some organic substances exist in the anaerobic ammonia oxidation tank 18. Thus, by using the adhesion / entrapping carrier 28 in which the nitrifying bacteria and the anaerobic ammonia oxidizing bacteria are retained, the nitrogen-containing wastewater can be efficiently treated in one tank of the anaerobic ammonia oxidizing tank 18. .
(F-3) FIG. 6 shows a wastewater treatment apparatus 40 according to the third embodiment of the present invention, which is a modification of FIG.

The nitrogen-containing wastewater containing at least ammonia flows into the nitrification tank 16 at the subsequent stage via the anaerobic ammonia oxidation tank 18. The nitrous acid and / or nitric acid generated by the nitrification reaction in the nitrification tank 16 is returned to the anaerobic ammonia oxidation tank 18 via the return pipe 32. Thereby, in the anaerobic ammonia oxidation tank 18, the ammonia flowing in via the raw water pipe 12 and the nitrous acid and / or nitric acid returned from the nitrification tank 16 via the return pipe 32 are simultaneously denitrified. Also in this case, nitric acid is used as a substrate after being converted to nitrous acid by the above-described bioreduction.
(F-4) FIG. 7 shows the wastewater treatment apparatus 50 according to the fourth embodiment of the present invention, and shows the apparatus configuration when there is too much organic matter in the nitrogen-containing wastewater.

As shown in FIG. 7, a part of the nitrogen-containing wastewater containing a large amount of organic substances in addition to ammonia flows into the nitrification tank 16 through the inflow path 14A of the branch pipe 14 branched from the raw water pipe 12, and the remaining The nitrogen-containing wastewater flows into the anaerobic ammonia oxidation tank 18 via the denitrification tank 34. In the denitrification tank 34, a fixed bed 36 of heterotrophic denitrifying bacteria is provided, and nitric acid is reduced to nitrous acid using the organic matter as a hydrogen donor, and the C / N ratio is lowered by consumption of the organic matter by this reduction. The outflow passage 14B of the branch flow passage 14 is divided into two branch pipes, the first branch pipe 14C is connected to the denitrification tank 34, and the second branch pipe 14D is connected to the anaerobic ammonia oxidation tank 18. As a result, nitrite and nitric acid are generated by the nitrification reaction in the nitrification tank 14, and a part of the generated nitrification liquid containing nitrous acid and nitric acid is transferred to the denitrification tank 34 via the first branch pipe 14C. It flows in and flows into the anaerobic ammonia oxidation tank 18 through the denitrification tank 34, and the remaining nitrification liquid flows directly into the anaerobic ammonia oxidation tank. In the denitrification tank 34, nitric acid is reduced to nitrous acid using the organic substance as a hydrogen donor, so that the organic substance in the nitrogen-containing wastewater is reduced in the denitrification tank 34. In the anaerobic ammonia oxidation tank 18, nitrate is reduced by heterotrophic denitrifying bacteria using the remaining organic matter as a hydrogen donor, and nitrous acid, which is a substrate for anaerobic ammonia oxidizing bacteria, is generated. Thereby, even if it is a case where there is too much organic substance in nitrogen-containing wastewater, the anaerobic ammonia oxidation reaction in the anaerobic ammonia oxidation tank 18 can be performed appropriately. The retention of heterotrophic denitrifying bacteria in the denitrification tank 34 is not limited to a fixed bed. In addition, in the denitrification tank 34 in the wastewater treatment apparatus described below, the retention mode of heterotrophic denitrifying bacteria is omitted.
(F-5) FIG. 8 shows a wastewater treatment apparatus 60 according to the fifth embodiment of the present invention, which is another aspect of the apparatus configuration when there is too much organic matter in the nitrogen-containing wastewater.

  As shown in FIG. 8, the nitrogen-containing wastewater containing a large amount of organic substances in addition to ammonia flows into the anaerobic ammonia oxidation tank 18 via the denitrification tank 34. Further, a nitrification tank 16 is provided at the subsequent stage of the anaerobic ammonia oxidation tank 18, and a part of the nitrification liquid from the nitrification tank 16 is returned to the denitrification tank 34 and the anaerobic ammonia oxidation tank 18 through the return pipe 32. .

According to this apparatus configuration, in the denitrification tank 34, nitric acid in the nitrification liquid returned from the nitrification tank 16 is reduced to nitrous acid using organic substances in the nitrogen-containing wastewater as hydrogen donors, and organic substances in the nitrogen-containing wastewater are reduced. To do. The remaining organic matter and the produced nitrous acid flow into the anaerobic ammonia oxidation tank 18 together with the ammonia in the nitrogen-containing wastewater, and the remaining organic matter in the nitrification solution is reduced as a hydrogen donor to produce nitrous acid. Then, ammonia and nitrous acid are simultaneously denitrified by anaerobic ammonia oxidizing bacteria. The ammonia remaining in the anaerobic ammonia oxidation tank 18 is nitrified in the nitrification tank 16, and a part of the nitrification liquid is returned to the denitrification tank 34 and the anaerobic ammonia oxidation tank 18 as described above. Therefore, the ammonia concentration remaining in the treated water can be reduced.
(F-6) FIG. 9 is a wastewater treatment apparatus 70 according to the sixth embodiment of the present invention, and shows the apparatus configuration when the amount of organic matter in the nitrogen-containing wastewater is too small. That is, the organic substance supply tank 38 for supplying organic substances to the anaerobic ammonia oxidation tank 18 is provided in the apparatus configuration of the wastewater treatment apparatus 10 described in FIG. Thereby, even when the organic substance density | concentration in nitrogen-containing wastewater is low, C / N ratio which is ratio of the organic carbon amount C in the anaerobic ammonia oxidation tank 18 and the total nitrogen amount N is 0.1-3, more Since it can set to the range of 0.2-1 preferably, the denitrification processing performance can be improved as demonstrated in FIG.
(F-7) FIG. 10 shows a wastewater treatment apparatus 80 according to the seventh embodiment of the present invention, which is another aspect of the apparatus configuration when the amount of organic matter in the nitrogen-containing wastewater is too small.

As shown in FIG. 10, a part of the nitrogen-containing wastewater containing ammonia passes through a raw water pipe 12 and passes through a multi-stage nitrite type nitrification tank 16A, 16B, 16C (FIG. 10 is three stages). While flowing into the anaerobic ammonia oxidation tank 18, the remainder of the nitrogen-containing wastewater flows directly into the anaerobic ammonia oxidation tank 18 via the branch pipe 14. A nitrite type nitrifying bacterium is introduced as a entrapping immobilization carrier 40 into each nitrification tank 16A, 16B, 16C. Further, an organic substance supply tank 38 for supplying organic substances to the anaerobic ammonia oxidation tank 18 is provided. As a result, ammonia in the nitrogen-containing wastewater is converted into nitrous acid by the multi-stage nitrite type nitrification tank 16 and flows into the anaerobic ammonia oxidation tank 18. In the anaerobic ammonia oxidation tank 18, nitrous acid flowing from the third-stage nitrification tank 16 </ b> C and ammonia flowing from the branch pipe 14 are simultaneously denitrified. In this denitrification reaction, the C / N ratio in the anaerobic ammonia oxidation tank is set in the range of 0.1 to 3 and more preferably in the range of 0.2 to 1 with the organic material supplied from the organic material supply tank.
(F-8) FIG. 11 shows a variation of FIG. 6 in which a nitrification tank 16 is provided at the rear stage of the anaerobic ammonia oxidation tank 18 in a wastewater treatment apparatus 90 according to an eighth embodiment of the present invention. That is, the nitrification liquid from the nitrification tank 16 is once sent to the sedimentation basin 42 and returned from the sedimentation basin 42 to the anaerobic ammonia oxidation tank 18 together with the return sludge.

  (F-9) FIG. 12 shows a variation of FIG. 8 in which a denitrification tank 34, an anaerobic ammonia oxidation tank 18, and a nitrification tank 16 are provided in a wastewater treatment apparatus 100 according to the ninth embodiment of the present invention. The nitrification liquid from the tank 16 is once sent to the settling tank 42 and returned to the anaerobic ammonia oxidation tank 18 together with the returned sludge from the settling tank 42.

Example 1
In Example 1, nitrogen-containing wastewater was treated using the wastewater treatment apparatus 10 of the present invention described in FIG.

Table 3 shows the composition and mixing ratio of the accumulated sludge and the like used in the production of the entrapping immobilization support held in the anaerobic ammonia oxidation tank. It has been confirmed by the FISH method that this accumulated sludge is sludge containing 40% or more of nine types of anaerobic ammonia oxidizing bacteria having a specific growth rate of 0.39 day ⁻¹ or more accumulated by the accumulation method described above.

過硫酸カリウムを添加することにより、上記組成はゲル化し、このゲルを３ｍｍ角の大きさに成形し、包括固定化担体として嫌気性アンモニア酸化槽に投入した。

By adding potassium persulfate, the above composition gelled, this gel was formed into a 3 mm square size, and charged into an anaerobic ammonia oxidation tank as a entrapping immobilization carrier.

  The test conditions are as follows.

  -The waste water used contained ammonia nitrogen concentration of 90-120 mg / L and organic substances containing 10-30 mg / L as BOD.

  The flow rate distribution ratio between the nitrogen-containing wastewater nitrification tank and the anaerobic ammonia oxidation tank was set to 1.4: 1.

  -The nitrification tank was filled with a contact filter medium to hold nitrite-type nitrifying bacteria, and the residence time was 8 hours.

  -The entrapping immobilization support was filled in an anaerobic ammonia oxidation tank at a filling rate of 20%, and the residence time was 2 hours.

  -The anaerobic ammonia oxidizing bacteria were stirred at a low speed by mechanical stirring.

  As a result of continuous treatment under the above test conditions, stable denitrification treatment was performed after acclimatization for one month from the start of operation, and the total nitrogen concentration of the treated water changed at a low level of 4 to 10 mg / L.

(Example 2)
In Example 2, nitrogen-containing wastewater was treated using the wastewater treatment apparatus of the present invention described in FIG. As the entrapping immobilization support for anaerobic ammonia-oxidizing bacteria introduced into an anaerobic ammonia-oxidizing tank equipped with an air aeration tube, one having the same composition as in Table 3 was used.

  The test conditions are as follows.

  -The used waste water contained ammonia nitrogen concentration 90-120 mg / L, and used what contained organic substance 10-30 mg / L as BOD.

  -The residence time of the anaerobic ammonia oxidation tank was 5 hours.

  -The filling rate of the entrapping immobilization support charged into the anaerobic ammonia oxidation tank was 20%.

  -Before the start of operation, nitrified sludge containing nitrite-type nitrifying bacteria was introduced into an anaerobic ammonia oxidation tank so as to be 1000 mg / L.

  -Air was aerated from an air aeration pipe while stirring at low speed by mechanical stirring in the anaerobic ammonia oxidation tank so that the dissolved oxygen concentration in the anaerobic ammonia oxidation tank was 0.1 to 0.5 mg / L.

  As a result of continuous treatment under the above test conditions, stable denitrification treatment was performed after acclimatization for one month from the start of operation, and the total nitrogen concentration of the treated water changed at a low level of 4 to 8 mg / L.

(Example 3)
In Example 3, the wastewater treatment apparatus of the present invention described with reference to FIG. 4 was used, and the nitrogen-containing wastewater was treated without using the entrapping immobilization support.

In the test, two wastewater treatment devices of FIG. 4 are prepared, and the concentration of the anaerobic ammonia oxidizing bacteria is 4 × 10 ⁶ (cells / mL) in the anaerobic ammonia oxidizing tank of the first device. Accumulated sludge was charged in the form of self-granulation. In addition, the second apparatus has self-accumulated sludge so that the concentration of anaerobic ammonia-oxidizing bacteria is 4 × 10 ⁶ (cells / mL) in the anaerobic ammonia-oxidizing tank as in the first apparatus. In addition to charging in the form of granulation, a sponge carrier was charged at the same time as the charging, and the self-granulated product was adhered and fixed to the sponge carrier. Other conditions are the same as in the first embodiment.

  As a result of continuous treatment under the above conditions, after one month of acclimatization from the start of operation, stable denitrification treatment is performed, and in the first device, the total nitrogen concentration of treated water changes at a low level of 10 to 13 mg / L, In the second apparatus, the total nitrogen concentration remained at a low level of 10 to 15 mg / L.

Example 4
About each of the waste water treatment apparatus of Example 1, and the 1st apparatus and 2nd apparatus in Example 3, when the high load operation was performed continuously, the denitrification speed of Table 4 was obtained. That is, in Example 1, when the entrapping immobilization support is introduced into the anaerobic ammonia oxidation tank, when the first apparatus of Example 3 is charged with self-granulation, the second apparatus of Example 3 is self-generated. This is a case where the particles are adhered to a sponge carrier.

表４から分かるように、包括固定化担体、自己造粒、付着担体の何れの脱窒速度も、これまで報告されている嫌気性アンモニア酸化細菌の脱窒速度よりも高い脱窒速度を示した。この結果は、比増殖速度０．３９日^-1以上の嫌気性アンモニア酸化細菌を集積培養した集積汚泥を使用したことに起因するものであり、この集積汚泥を使用することで高速脱窒を行うことができることが実証された。

As can be seen from Table 4, the denitrification rates of the entrapping immobilization support, self-granulation, and adherent support were higher than the denitrification rates of anaerobic ammonia-oxidizing bacteria reported so far. . This result is attributed to the use of accumulated sludge obtained by accumulating anaerobic ammonia-oxidizing bacteria having a specific growth rate of 0.39 day- ¹ or more, and high-speed denitrification is performed by using this accumulated sludge. It has been demonstrated that it can.

  Moreover, in order to obtain a high denitrification rate from repeated test results, it is not necessary to include all of SEQ ID NOs: 1 to 9 in the above sequence listing, and it is necessary to include at least one type of sequence. I understood. However, it has been found that it is more preferable to occupy 40% or more of the density in the accumulated sludge with anaerobic ammonia-oxidizing bacteria having nine base sequences.

  Incidentally, in order to treat this type of nitrogen-containing wastewater by the conventional nitrification / denitrification method, the residence time of the nitrification tank is 4 hours, and the residence time of the denitrification tank is 4 hours, which increases the size of the apparatus. Further, not only a large amount of air is required to nitrify the entire amount of ammonia in the nitrification tank, but a large amount of methanol is required in the denitrification tank.

On the other hand, in the wastewater treatment method of the present invention using anaerobic ammonia oxidizing bacteria having a specific growth rate of 0.39 day- ¹ or more, it is not necessary to nitrify the entire amount of ammonia, and the amount of air can be greatly reduced. There is also no need to add. In addition, the apparatus can be made compact.

Explanatory drawing explaining the culture | cultivation method which accumulates and cultures anaerobic ammonia-oxidizing bacteria with a specific growth rate of 0.39 day ^-1 Relationship between the number of anaerobic ammonia-oxidizing bacteria with a specific growth rate of 0.39 day- ¹ or more and the denitrification rate Relationship diagram between C / N ratio and total nitrogen removal rate The block diagram of the waste water treatment apparatus of the 1st Embodiment of this invention The block diagram of the waste water treatment apparatus of the 2nd Embodiment of this invention The block diagram of the waste water treatment apparatus of the 3rd Embodiment of this invention The block diagram of the waste water treatment apparatus of the 4th Embodiment of this invention The block diagram of the waste water treatment apparatus of the 5th Embodiment of this invention The block diagram of the waste water treatment apparatus of the 6th Embodiment of this invention The block diagram of the waste water treatment apparatus of the 7th Embodiment of this invention The block diagram of the waste water treatment equipment of the 8th Embodiment of this invention The block diagram of the waste water treatment apparatus of the 9th Embodiment of this invention

Explanation of symbols

DESCRIPTION OF SYMBOLS 10, 30, 40, 50, 60, 70, 80, 90, 100 ... Waste water treatment apparatus, 12 ... Raw water piping, 14 ... Branch piping, 16 ... Nitrification tank, 18 ... Anaerobic ammonia oxidation tank, 20 ... Anaerobic ammonia Oxidizing bacteria inclusion immobilization carrier, 22 ... screen, 24 ... treated water piping, 26 ... air aeration pipe, 28 ... adhesion / entrapping carrier, 32 ... return piping, 34 ... denitrification tank, 36 ... heterotrophic denitrifying bacteria Fixed bed, 38 ... Organic substance supply tank, 40 ... Entrapment immobilization support for nitrifying bacteria, 42 ... Sedimentation basin [Sequence Listing]
Sequence listing

<110> Hitachi plant engineering & construction co., Ltd
isaka kazuichi
sumino tatsuo
tsuneda satoshi
<120> Waste water Treatment Method and apparatus
<130> HP2006-007
<160> 9
<170> PatentIn version
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<210> 9
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Claims (13)

In a wastewater treatment method for treating nitrogen-containing wastewater containing at least ammonia in a treatment tank using anaerobic ammonia-oxidizing bacteria that performs denitrification using nitrous acid and ammonia as substrates,
In the said processing tank, the wastewater treatment method characterized by making the accumulation sludge which carried out the accumulation culture | cultivation of the anaerobic ammonia oxidation bacteria of the specific growth rate 0.39 day- ¹ or more from a seed sludge contact the said nitrogen-containing wastewater. The accumulated sludge is accumulated and cultured by holding the seed sludge in a culture tank and passing a culture solution containing at least the substrate at a dilution rate of 0.39 to 24 days- ^1. The wastewater treatment method according to claim 1. The wastewater treatment method according to claim 1 or 2, wherein the accumulated sludge contains 10 ⁵ cells / mL or more of the anaerobic ammonia-oxidizing bacteria.   The wastewater treatment according to any one of claims 1 to 3, wherein the accumulated sludge is retained in the treatment tank in any form of an adhesion immobilization carrier, a entrapping immobilization carrier, and a self-granulated product. Method.   The wastewater treatment method according to any one of claims 1 to 4, wherein a C / N ratio, which is a ratio of an organic carbon amount C and a total nitrogen amount N in the treatment tank, is 0.1 or more and 3 or less. .   The wastewater treatment method according to any one of claims 1 to 5, wherein the treatment tank is treated under anaerobic conditions.   The entrapping immobilization support for the anaerobic ammonia-oxidizing bacteria and nitrifying sludge containing nitrifying bacteria are introduced into the treatment tank, and the treatment is performed under aerobic conditions in the treatment tank. The wastewater treatment method according to any one of Items 1 to 5. In a wastewater treatment apparatus that treats nitrogen-containing wastewater containing at least ammonia in a treatment tank using anaerobic ammonia-oxidizing bacteria that performs denitrification using nitrous acid and ammonia as substrates,
The waste water treatment apparatus, wherein the treatment tank is filled with an accumulated sludge in which anaerobic ammonia-oxidizing bacteria having a specific growth rate of 0.39 day ^-1 or more are accumulated and cultured from the seed sludge.   The wastewater treatment apparatus according to claim 8, wherein the wastewater treatment apparatus is provided with a nitrification tank for converting a part of ammonia in the nitrogen-containing wastewater into nitrous acid and / or nitric acid.   The wastewater treatment apparatus according to claim 8 or 9, wherein the wastewater treatment apparatus is provided with a heterotrophic denitrification tank that reduces nitric acid to nitrous acid.   The wastewater treatment apparatus according to any one of claims 8 to 10, wherein the wastewater treatment apparatus is provided with an organic substance addition means for adding an organic substance into the treatment tank.   The wastewater treatment apparatus according to any one of claims 8 to 11, wherein the treatment tank is treated under anaerobic conditions.   The entrapping immobilization support for the anaerobic ammonia-oxidizing bacteria and nitrified sludge are introduced into the treatment tank, and air aeration means for aerating air is provided in the treatment tank. The wastewater treatment apparatus according to any one of 11.

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