KR20130003238A - The method and treatment process of wastewater containing organic matter and nitrogen compounds-livestock wastewater, digestive wastewater, food wastewater - Google Patents

Abstract

PURPOSE: A method and apparatus for treating wastewater containing organic material and nitrogen components are provided to prevent environmental contamination by treating organic wastewater into a condition suitable for directly discharging into a river. CONSTITUTION: A method and apparatus for treating wastewater containing organic material and nitrogen components comprises: a step of anaerobic treating waste water for 1-2 hours; a step of introducing first treated water into an oxygen-free tank and stirring the same for 1-2 hours; a step of introducing the second treated water into an aerobic tank and aerobic treating the same; a step of introducing the third treated water into a precipitation tank and leaving the same for 2-4 hours for separating into liquid supernatant and solid sludge; a step of introducing the supernatant into a denitrification tank and denitrificating the same for 1-4 hours; and a step of introducing the fourth treated water into the aerobic tank and aerobic treating the same. [Reference numerals] (S10) First treating step of anaerobically treating waste liquid or wastewater through precipitation and degassing; (S20) Second treating step of stirring the anaerobically treated waste liquid or wastewater in an anoxic bath; (S30) Third treating step of aerobically treating aerating the stirred waste liquid or wastewater; (S40) Precipitating step of separating the aerobically treated waste liquid or wastewater into supernatant and solid sludge; (S50) Fourth treating step of sulfating and denitrifying supernatant using sulfating and denitrifying microorganisms; (S60) Fifth treating step of aerating sulfated and denitrified waste liquid or wastewater

Description

The method and treatment process of wastewater containing organic matter and nitrogen compounds-livestock wastewater, digestive wastewater, food wastewater}

The present invention relates to an apparatus for treating livestock wastewater, digestive waste liquid, and negative wastewater containing organic substances and nitrogen components, and a method of treating the same. Livestock wastewater, digestive waste, and negative wastewater containing organic and nitrogen components to treat high concentration organic wastewater such as digested wastewater, effluents leaching from food waste, livestock wastewater, and direct discharge into sewage treatment plant or water system A processing apparatus and a processing method thereof.

For livestock wastewater containing high concentrations of organic matter and nitrogen, about 0.5% of total wastewater generated in Korea, but the pollutant loading rate on water systems is 18%, causing water degradation and eutrophication in streams and lakes. Not only does it reduce the availability of water, it also threatens drinking water sources and accelerates soil and groundwater contamination. In addition, the odors and pests that are produced are worsening the living environment of nearby residents and are subject to civil complaints.

As the progress of anaerobic digestion technology that can produce energy while processing organic waste such as livestock manure, there is a problem of the treatment of digestive waste liquid discharged after anaerobic digestion.

Digestive waste liquid contains high concentration of organic matter and nitrogen like livestock waste water, so it is recommended to be used as liquid fertilizer, but there are some problems in using whole amount as liquid fertilizer.

Therefore, the use of liquid fertilization, some of the ways to treat the water, but the water treatment process has not been completed yet, various local water treatment processes are being studied.

The digestive waste liquid after anaerobic digestion has similar characteristics to the livestock wastewater, but unlike the livestock wastewater discharged after solid-liquid separation of powder and furnace, the livestock waste is decomposed and removed to some extent through the anaerobic digestion process. Compared with the digestive waste fluid, the amount of remaining hardly decomposable organic matters is higher and the nitrogen concentration is higher.

As a result, the anaerobic digestion wastewater is more difficult to treat than livestock wastewater and, unlike livestock wastewater, which has been developed for a long time since it has been treated for a long time, it is developed under the name of energyization of organic waste. Digestion technology development is progressing recently, the development of technology to treat digestive waste liquid can be said to have begun.

Such livestock wastewater treatment method, which is the most similar to digestive waste liquid in terms of properties, includes liquid corrosion method, HBR, BIOSUF, B3 method, SBR method, and natural purification method. However, nitrogen and phosphorus removal efficiency is insufficient, Since it takes a long time to remove the nitrogen and nitrogen components, the facility investment and operating costs are high, and the operation is difficult.

Regarding the reduction of organic matter, the treatment method is studied in many areas, and if the sufficient residence time and the proper inflow concentration are maintained, organic removal efficiency can be achieved to some extent, but this has a direct effect on facility installation cost and operation management cost. Fewer places

Also, eutrophication agents and coloring problems such as nitrogen and phosphorus are difficult to achieve high removal efficiency in the subsequent high-level treatment process. This is also relative to cost.

In general, COD _Cr concentration in animal meal is about 180,000 to 250,000mg / l, and urinary COD _Cr concentration is 10,000 to 20,000mg / l, which is about 20 times difference.Ammonia nitrogen is 5,000 ~ 10,000mg / l, urine 4,000 ~ 5,000 ㎎ / ℓ shows about twice the difference.

The livestock wastewater treatment plant is based on the separation of urine and urine, and when the inflow of public treatment plant does not separate sewage and urine, it is not allowed to bring in high BOD concentrations.

Food waste is a representative organic waste, and its amount is continuously increasing due to the increase of food consumption and the separation of food collection due to the improvement of income level. Moreover, since landfilling has been banned since 2005, the process becomes more difficult (Ministry of Environment, 2007). Food wastes vary in composition from source to source.

In the case of water content, about 90% of wastes from agricultural wholesale markets, about 80% of wastes from homes, and about 77% of wastes from restaurants. Organic matter content is 88% in restaurants, 83% in homes, 77% in agricultural wholesale markets, and NaCl content is 4.8% in homes, 3.4% in restaurants, and 0.8% in agricultural wholesale markets (agriculture). Promotion Agency, 1999). Salinity is the most important ingredient in composting, and is currently controlled by hydrolysis in the pretreatment stage, but increases in anaerobic digestion and effluent (digestive desorption liquid caused by solid-liquid separation after digestion: food waste waste). There are disadvantages.

As described above, the biggest difficulty in recycling food waste is the treatment of effluent. According to the Ministry of Environment's data, the amount of wastewater is increasing every year, and treatment is required at sewage treatment plants for discharge of public waters, but sewage treatment plants mainly treat negative wastewater from public facilities due to compliance with discharge water quality standards. The company has discharged wastewater containing 8% of solids after separation of solids, but since 2012, the dumping of ocean dumping has been banned.

In recent years, marine emissions have been gradually reduced worldwide due to marine pollution, and Korea has been strengthening marine emission standards in accordance with the application of international regulatory standards, while also promoting accession to the London Convention and the 1996 Protocol. If regulations on ocean emissions are tightened, it is necessary to completely change the treatment practices performed by private companies.

In order to treat such a sewage treatment plant, the sewage treatment plant capacity should be increased as the load of the sewage treatment plant is increased, and the wastewater treatment facility should be perfectly equipped to treat the treatment plant without increasing its capacity.

However, at present, there are only a few technologies in Korea that can match the water quality for sewage treatment, and there are no technologies that can handle the discharge of public waters. Of course, if the facility investment cost is sufficient, it can be handled to some extent by combining various technologies, but it is difficult to make a lot of investment.

In the treatment of organic wastewater such as digestive waste liquid, drinking wastewater and livestock wastewater, the anaerobic treatment method is the most effective among the main treatment techniques for removing organic matter. However, the anaerobic treatment method is insufficient to remove nitrogen and phosphorus, and if the influent of the anaerobic treatment method contains a high concentration of ammonia nitrogen, there is a problem that the treatment efficiency is lowered due to the increase of the preammonia (FA) concentration.

The aerobic treatment methods include activated sludge method, activated sludge method (AO method, A2O method, membrane separation activated sludge method, etc.), biofilm method (contact oxidation method, rotating disc method, etc.), batch activated sludge method, and oxidative ball method (畜産 糞尿). Establishment and Determination Guide Block, Deposition, p. 13, 2004). The aerobic treatment method requires an organic matter (BOD) concentration of more than 3,000 mg / L, an organic matter and nitrogen ratio (C / N ratio) of 5 or less, or more than 10, resulting in a very low treatment efficiency, requiring a long residence time and a large site. There is a problem.

In the advanced treatment of nitrogen and phosphorus, nitrogen mainly uses biological treatment technology and phosphorus uses chemical flocculation sedimentation technology.

Nitrogen removal is predominantly a biological treatment that combines nitrification with autotrophic microorganisms and denitrification with heterotrophic microorganisms. In this case, nitrification is the process in which ammonia (NH ₄ ⁺ -N) is converted to nitrite nitrogen (NO ₂ ^-- N) or nitrate nitrogen (NO ₃ ^-- N) by an autotrophic microorganism, from ammonia to nitrous acid. when it is oxidized, and microorganisms such as Nitrosomonas, Nitrosococcus, Nitrosobacillus involved, when it is oxidized to nitrite from nitric acid are involved, such as Nitrobacter, Nitrosocystis.

The nitrification requires oxygen, and a large amount of nitrifying microorganisms must be secured and maintained in the reactor. In addition, a large amount of alkalinity is required, so a pH buffer is required to control the lowering pH. Temperature, BOD / N ratio, and ammonia concentration also influence nitrification.

Denitrification is carried out by heterotrophic microorganisms such as Pseudomonas , Bacillus and Micrococcus in the anoxic state in which there is no dissolved oxygen (DO) and nitrous or nitrite nitrogen is released into nitrogen gas (N ₂ ). The process of conversion. Heterotrophic denitrification requires an organic carbon source as an electron donor, so if an organic carbon source is low, an organic carbon source such as methanol should be added. However, in the case of methanol addition, it is difficult to control the proper amount of addition, and methanol remains in the treated water due to the toxicity of methanol itself, which causes secondary contamination. The theoretical amount of methanol required is more than three times the amount of nitrogen to be treated, but from the actual field operation results, it is known that an average of 6.5 times is required, from 3 to 10 times.

Most biological treatments that combine nitrification with autotrophic microorganisms and denitrification with heterotrophic microorganisms consist mostly of an anaerobic tank-aerobic tank and circulate the wastewater to cause denitrification in the aerobic tank and nitrification in the aerobic tank. However, this method requires a separate installation of the reactor, so a large installation site is required and the aerobic capacity must be increased. In order to obtain stable treated water with a small reaction tank volume, a method of filling activated sludge or a carrier immobilized with nitrifying or denitrifying bacteria is also used instead of suspended activated sludge.

However, there are disadvantages in that the carrier price is high and the microbial membrane is formed on the surface of the carrier, and after a certain period of time, it is precipitated by load, or the carrier is blocked, so that the waste water or air does not pass through the carrier and is anaerobic. This problem is caused by the large size of the carrier pores.

Denitrification using sulfur, recently attracting attention, is Thiobacillus In the process of oxidizing sulfur, the sulfated microorganism represented by denitrificans converts the nitrate or nitrite nitrogen into nitrogen gas by using the oxygen component combined with the nitrate nitrogen or nitrite nitrogen. This reaction removes nitrogen from the water.

Sulfation denitrification takes place in the absence of oxygen and in the absence of oxygen in the presence of nitrate nitrogen or nitrite nitrogen. Chemistry denitrifying microorganisms are sulfate absolute chemical autotrophic microorganisms ^{_{CO 2, HCO 3 -, CO}} 3 2 - because the arms, such as the growth carbon using a carbon source, there is no need to input by an organic carbon source such as methanol.

In addition, as a result of comparing the cost of sulfur compounds as hydrogen acceptors by the chemical cost per electron equivalent in the denitrification reaction by T. denitrificans , it is reported that S ^O is the most economic hydrogen donor (Bisogni, JJr & Driscoll, CT Jr.). Denitrification using thiosulfate and sulfide, J. Environ.Eng. Div. Proc.ASCE, Vol.103, p. 593-604 (1977).

These, S ^O is resource rich, low-cost prices, good handling, easy to save, but the advantages of non-toxic, there is a disadvantage does not dissolve readily in water. In addition, sulfated denitrification microorganisms are known to be difficult to accumulate and solid-liquid separation of microorganisms due to their cohesiveness. In addition, sulphate ions, the final product of the sulphation reaction, lower the pH, and when the pH is 5.5 or less, there is a problem in that the denitrification reaction is inhibited and the alkalinity must be continuously added.

There is a technology developed by our company (Patent No. 0503134) to solve the above-mentioned problem of the sulfate denitrification method, and this technique is achieved by using an integrated carrier prepared by melting sulfur and alkaline substances. It solves all the problems caused by the process.

In drinking water and livestock waste water, brown color derived from humic acid appears, which is hardly removed even after the first, second and third treatment. Fenton oxidation method, ozone treatment method, electrolysis method, etc. are used to remove the color, excessive treatment cost is a problem compared to the removal efficiency, such as chemical costs and electricity bills.

For this reason, there is an urgent need for an improved wastewater treatment apparatus and treatment method that is simple in structure and capable of purifying wastewater and wastewater to meet legal discharge criteria.

The present invention treats organic wastewater, such as livestock manure, food waste, sewage sludge alone or combined, and treats wastewater discharged during anaerobic digestion, drinking wastewater leaching from food waste, livestock wastewater, and high concentration organic wastewater such as livestock wastewater. Or for direct discharge into the water system.

In order to achieve the above object, the present invention is a treatment apparatus for treating wastewater or wastewater, such as livestock wastewater, digestive wastewater, negative wastewater, comprising a dehydrator for solid-liquid separation of the waste liquid or waste water, the solid-liquid separation A sediment is formed to separate and remove residual solids and organics by receiving waste liquid or waste water, and to form a degassing tank to remove high concentration of ammonia nitrogen by receiving clean supernatant present in the sedimentation tank. The first anaerobic tank is configured to receive the supernatant from which cattle are removed, and to remove the high concentration of organic matter contained in the supernatant. After conversion, some are removed by heterotrophic denitrification and others are sulfate denitrification By providing a nitrate or nitrite to the reaction vessel consisting of a microorganism to remove nitrogen characteristic of the livestock waste water containing organic matter and nitrogen components, the process of extinguishing the waste, the waste water apparatus and the sound processing method.

As described above, the present invention treats high concentration organic wastewater, such as live wastewater leaching from anaerobic digestion, effluents leaching from food waste, livestock wastewater, by combining organic wastes such as livestock manure, food waste and sewage sludge alone or in combination. It is a system to link sewage treatment plant or direct discharge to water system, and it has a useful effect to protect ecosystem and effectively preserve nature through proper wastewater treatment.

1 is a schematic configuration diagram showing a treatment apparatus for treating various wastewater according to the present invention;
2 is a flow chart showing a treatment method for treating various wastewater according to the present invention.

BRIEF DESCRIPTION OF THE DRAWINGS The above and other features and advantages of the present invention will be more apparent from the following detailed description taken in conjunction with the accompanying drawings, in which: FIG.

1 and 2, a treatment apparatus for treating various wastewater of the present invention relates to a treatment apparatus for treating waste liquid or wastewater, such as livestock wastewater, digestive wastewater, negative wastewater, dehydrator (10) And a precipitator 20 for separating and removing solids and organics, a degassing tank 30 for removing ammonia nitrogen, a first anaerobic tank 40 for removing high concentrations of organic matter, and a microbial reaction tank 50 for removing nitrogen. 100 is configured.

First, the dehydrator 10 is to solid-liquid waste liquid or waste water,

In addition, the settling tank 20 is configured to separate and remove the remaining solids and organics by receiving the solid-liquid separated waste liquid or waste water.

At this time, the dehydrator 10 is installed inside the settling tank 20.

When the organic wastewater such as digestive waste liquid, livestock wastewater, and negative wastewater flows into the dehydrator 10, the dehydrator 10 is configured to remove solids, total phosphorus, etc. by dehydration in the dehydrator 10.

On the other hand, the degassing tank 30 is configured to remove the high concentration of ammonia nitrogen by receiving the clean supernatant present in the settling tank 20.

In addition, the degassing tank 30 is configured to degas and remove ammonia nitrogen when the supernatant treated to a solids concentration suitable for anaerobic reaction by further treating the solids (SS) in the settling tank 20.

Then, the first anaerobic tank 40 is configured to remove the high concentration of organic matter contained in the supernatant by receiving the supernatant water from which the ammonia nitrogen is removed through the degassing tank 30.

The treated water treated in the degassing tank 30 is introduced into the first anaerobic tank 40 to decompose organic matter components (COD _Cr , COD _Mn , BOD) by anaerobic microorganisms (Granules) to form CH ₄ and CO ₂ gas. Is generated.

In addition, the microbial reaction tank 50 receives the supernatant from which high concentration organic matter is removed from the first anaerobic tank 40 and converts residual ammonia nitrogen to nitrate nitrogen or nitrite nitrogen, and partly by heterotrophic denitrification. The remainder is configured to remove nitrate nitrogen or nitrite nitrogen with nitrogen gas by a sulphate denitrification reaction in the sulphate denitrification tank 51 in which the sulphate denitrification bacteria are predominant.

Here, the microbial reaction tank 50 is composed of a sulfate denitrification tank 51 in which the sulfated denitrification bacteria dominates.

A second anaerobic tank 52 is connected to the sulfate denitrification tank 51 and includes a first stirrer 52a.

On the other hand, the treated water treated in the first anaerobic tank 40 is introduced into the second anaerobic tank 52 of the microbial reaction tank 50, where the organic material is partially removed and the phosphorus component is configured to be discharged to the outside of the sludge.

In addition, the anaerobic tank 53 is connected to the second anaerobic tank 52 and includes a second stirrer 53a.

At this time, the treated water treated in the second anaerobic tank 52 is introduced into the oxygen-free tank 53 is configured to denitrify the nitrogen nitrate with nitrogen gas by using the organic matter remaining by the heterotrophic denitrification microorganism.

In addition, the aerobic tank 54 is connected to the anoxic tank 53 and includes an aeration nozzle.

The treated water of the anoxic tank 53 is introduced into the aerobic tank 54, the residual organic matter is decomposed by the aerobic microorganisms, the ammonia nitrogen is nitrified to nitrate nitrogen or nitrite nitrogen, the phosphorus component released from the anaerobic tank is an aerobic microorganism Absorbed in the excess sludge to remove the phosphorus component is configured.

On the other hand, the settling tank 55 is connected to the aerobic tank 54, and the first connection passage 56 is connected to supply the supernatant water obtained in the settling tank 54 to the sulfate denitrification tank 51.

In addition, the treated water treated in the aerobic tank 54 is introduced into the sulphate dedusting tank 51 and the remaining nitrate nitrogen or nitrite nitrogen is denitrated by nitrogen gas by the sulphate denitrification microorganism as an independent nutrient.

In this case, the treated water treated in the desulfurization tank 51 is configured to be discharged by removing the chromaticity by chemical coagulation or ozone treatment in the decolorization tank 57.

Referring to the operation and the embodiment of the present invention configured as described above are as follows.

As shown in Figure 1 and 2, by using the apparatus 100 for treating wastewater or wastewater, such as livestock wastewater, digestion wastewater, negative wastewater, the residual organic matter and nitrogen to the effluent standard to the wastewater or wastewater treatment method The first treatment step (S10), the secondary treatment step (S20), the third treatment step (S30), the precipitation step (S40), the fourth treatment step (S50), the fifth treatment step (S60).

First, the first treatment step (S10) is a second through which the inflow of the waste liquid or wastewater through the sedimentation and degassing process through the sedimentation tank 20, the degassing tank 30, the first anaerobic tank 40 sequentially It is introduced into the anaerobic tank 52 and stirred in the second anaerobic tank for 1 to 2 hours to anaerobic treatment.

Thereafter, the secondary treatment step (S20) is a step of introducing the primary treated water into the anaerobic tank while undergoing the primary treatment step (S10) to stir for 1 to 2 hours in the anoxic tank 52. .

Next, the tertiary treatment step (S30) is introduced into the aeration tank 53 while the secondary treatment water through the secondary treatment step (S20) into the aerobic tank 53 is rich in air or oxygen in the aerobic tank 53 Gas for 4 to 12 hours Aeration and aerobic treatment.

Subsequently, the precipitation step (S40) is introduced into the sedimentation tank 54 by the third treated water while passing through the third treatment step (S30) to leave the third treated water for 2 to 4 hours This is a step of separating the liquid supernatant and the solid sludge.

In addition, the fourth treatment step (S50) is a step of introducing the supernatant discharged from the precipitation step (S40) into the sulfate denitrification tank 51 and desulfurization and denitrification by the sulfate denitrification microorganism for 1 to 4 hours. .

Finally, the fifth treatment step (S60) introduces the fourth treated water back into the aeration tank (53) to allow air or oxygen-rich gas in the aeration tank (54) for 4 to 12 hours. Aeration and aerobic treatment.

At this time, when the supply flow rate of the inflow water is not constant and the fluctuation range of the flow rate is large, a part of the discharged fourth treated water is recycled to the aerobic tank 54 so that the purified water purification process of the microbial reaction tank 50 is performed rather than the purified water treatment. It is a step to lose.

An example in which the processing method using the processing apparatus 100 as described above is applied is as follows.

For example, in connection with a pilot plant that produces biogas by anaerobic digestion of pig manure discharged from pig farms, it operates a pilot plant that processes digestive waste liquid discharged from an anaerobic digester as shown in Table 1. The result was obtained.

Analysis item pH COD _Cr T-N NH3-N T-P TS unit - ㎎ / ℓ ㎎ / ℓ ㎎ / ℓ ㎎ / ℓ % Digestive waste 8.05 49,369 4,146 3,694 874 3.09

The condition was that the solid concentration after dehydrating the digestive waste liquid with the dehydrator 10 was about 3,000-4,000 mg / L, and the total nitrogen concentration was about 2,000 mg / L.

Thus, after treating the solid concentration in the settling tank 20 to 1,000 mg / L or less, deaeration and removal of ammonia nitrogen in the degassing tank 30, and flowed into the first anaerobic tank (40).

Here, the first anaerobic tank 40 is a method for removing high concentrations of organic matter by using microorganisms granulated anaerobic bacteria by a high-efficiency anaerobic treatment method, the solids concentration of raw water can be shown to be normal performance only less than 1,000mg / L. have.

At this time, the hydrogen ion concentration value was operated at pH 6.8 ~ 7.2, the temperature was maintained while maintaining at 35 ~ 37 ℃.

The organic matter removal efficiency of the method using the first anaerobic tank 40 was confirmed by operating with the inflow load concept represented by the ratio of the organic load flowing into the volume of the first anaerobic tank 40.

Then, the digestive waste liquid adjusted to a condition that is easy to be removed by anaerobic bacteria was transferred to the second anaerobic tank 52 by using a pump more than the inflow flow rate.

In addition, the digestive waste fluid introduced into the lower portion of the second anaerobic tank 52 removes organic matter while flowing a predetermined amount of granule layer in an upstream, and discharges the flow rate in which three phases (gas, liquid, solid) are separated through an upper settler. The rest was again introduced into the second anaerobic tank 52, mixed with the influent, and reintroduced into the sulfate denitrification tank 51.

Thus, the inflow load flowing into the desulfurization tank 51 was calculated based on the flow rate flowing into the adjustment tank, and the flow rate flowing into the first anaerobic tank 40 was operated at 1.5 times the inflow flow rate.

The average COD _Cr concentration of the ingested digestive fluid was 36,356 mg / l and the influent load was 15 kg / m 3 · D. The results are shown in Table 2.

Item COD _Cr  Removal rate Biogas Generation Methane gas content unit % ℓ / D % value 72 20.26 80

In addition, the first anaerobic tank 40 treated water was introduced into the J-PONT system (All Tech-In & Organics & Nitrogen Treatment System), which is a modified A ₂ O method.

Such, the treatment device 100 is added to the conventional anaerobic-anoxic-aerobic process (sulfurization and denitrification technology (Patent No. 10-0503134), and compared to the treatment capacity of the conventional method (about 80%) nitrogen The removal performance is characterized by 20% higher.

At this time, the process flow is [sulfur oxide denitrification-anaerobic-anoxic-aerobic], and the low nitrogen removal performance and the stable nitrogen removal performance pointed out as problems in the existing activated sludge method, activated sludge modification method, A ₂ O method, A ₂ O modification method, etc. It is difficult to maintain the removal efficiency, it is difficult to maintain a stable phosphorus removal performance, the large capacity of the processing system is required to solve the problems such as the need for a wide treatment site, the results are shown in Table 3.

Item enemy Effluent Removal rate unit ㎎ / ℓ ㎎ / ℓ % COD _Cr 2,055 113 94.5 COD _Mn 1,892 86 95.5 SS 324 40 87.7 T-N 877 58 93.4 T-P 85 22 74.1

In this way, the treatment apparatus 100 is treated in a chemical coagulation tank or ozone treatment tank for decolorization, and finally discharged to the water system or the sewage treatment plant linked processing.

Thus, the present invention is to treat high concentration organic wastewater, such as anaerobic wastewater, food waste generation wastewater (negative wastewater) and livestock wastewater, as described above, by treating such organic wastewater, sewage treatment plant linked treatment or water system There is a characteristic that can prevent the environmental pollution by water purification in a suitable condition for direct discharge.

In the above, the present invention has been illustrated and described by way of specific preferred embodiments, but the present invention is not limited to the above-described embodiments, and the present invention is not limited to the spirit of the present invention. Various changes and modifications can be made by those who have

10: dehydrator 20: sedimentation tank
30: degassing tank 40: first anaerobic tank
50: microbial reaction tank 51: sulfate denitrification tank
52: 2nd anaerobic tank 52a: 1st stirrer
53: anaerobic tank 53a: second stirrer
54: aerobic tank 55: sedimentation tank
56: first connection passage 57: decolorization tank
100: Processing device
S10: primary treatment stage S20: secondary treatment stage
S30: 3rd step S40: precipitation step
S50: 4th processing step S60: 5th processing step

Claims (4)

In the treatment apparatus for treating wastewater or wastewater to be treated, such as livestock wastewater, digestion wastewater, drinking water,
To constitute a dehydrator (10) for separating the waste liquid or waste water into a solid solution,
The solid-liquid separated waste liquid or waste water is supplied to constitute a sedimentation tank 20 for separating and removing residual solids and organic matter,
Constructing a degassing tank 30 to remove the high concentration of ammonia nitrogen by receiving clean supernatant water present in the settling tank 20,
The first anaerobic tank 40 is provided to receive the supernatant water from which the ammonia nitrogen is removed through the degassing tank 30 to remove the high concentration of organic matter contained in the supernatant water.
After receiving the supernatant from which the high concentration organic matter is removed from the first anaerobic tank 40, the remaining ammonia nitrogen is converted to nitrate nitrogen or nitrite nitrogen, and some are removed by heterotrophic denitrification, and the rest is sulphated and denitrified. Livestock wastewater, digestive waste liquid, drinking water containing organic matter and nitrogen components, characterized in that consisting of a microorganism reaction tank (50) for removing nitrate nitrogen or nitrite nitrogen by the method. The organic material according to claim 1, wherein the dehydrator (10) is installed inside the sedimentation tank (20) so that the waste liquid or waste water dewatered from the dehydrator (10) is configured to separate solids and organic matter from the sedimentation tank (20). Livestock wastewater, digestive waste liquid and effluent containing nitrogen and nitrogen. The method of claim 1, wherein the microbial reaction tank 50 is a sulfated denitrification tank 51 is formed by predominantly sulfated denitrification bacteria,
A second anaerobic tank 52 connected to the sulfate denitrification tank 51 and including a first stirrer 52a;
An anaerobic tank 53 connected to the second anaerobic tank 52 and including a second stirrer 53a;
An aerobic tank 54 connected to the anoxic tank 53 and including an aeration nozzle,
A settling tank 55 connected to the exhalation tank 54,
Livestock wastewater containing the organic matter and nitrogen components, digestion, comprising: a first connection passage 56 connected to supply the supernatant water obtained from the settling tank 54 to the sulphation denitrification tank 51 Wastewater, treatment equipment of negative wastewater. In the method of treating the waste liquid or waste water to the discharged water standard by using the apparatus for treating waste liquid or waste water such as livestock waste water, digestive waste liquid, negative waste water,
The second anaerobic tank is introduced through the sedimentation tank 20, the degassing tank 30, and the first anaerobic tank 40 in order to introduce into the second anaerobic tank 52 through which the inflow water of the waste liquid or wastewater, which has undergone precipitation and degassing, is passed through the air. Primary treatment step (S10) for anaerobic treatment by stirring for 1 to 2 hours in (52);
A second treatment step (S20) of introducing the first treated water treated as the first treatment step (S10) into the anoxic tank to stir for 1 to 2 hours in the anoxic tank (52);
Through the secondary treatment step (S20) to introduce the secondary treated water into the aerobic tank (53) by the air or oxygen-rich gas in the aerobic tank (53) for 4 to 12 hours Tertiary treatment step (S30) for aeration by aeration;
The tertiary treated water is introduced into the sedimentation tank 54 while passing through the tertiary treatment step (S30) to allow the tertiary treated water to stand for 2 to 4 hours to be separated into liquid supernatant and solid sludge. Precipitation step (S40);
A fourth treatment step (S50) of introducing the supernatant flowing out of the precipitation step (S40) into the sulfate denitrification tank 51 and performing sulfate denitrification by the sulfate denitrification microorganism for 1 to 4 hours; And
The fourth treated water is introduced into the aerobic tank (53) again to the aerobic treatment 53 to aeration process by aeration of air or oxygen-rich gas for 4 to 12 hours in the aerobic tank (S60) Livestock wastewater, digestive waste liquid, negative waste water containing a treatment method containing organic matter and nitrogen components.

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