JP2010253404A - Method and apparatus of denitrifying digested sludge separation liquid - Google Patents

Abstract

<P>PROBLEM TO BE SOLVED: To provide a method and an apparatus of denitrifying digested sludge separation liquid, by which a high nitrification activity can be kept without the deceleration of a nitrification speed and a stable denitrification can be performed. <P>SOLUTION: In the method of adding a polymer 6 to nitrogen-containing digested sludge 5 to separate solid and liquid and denitrifying obtained separation liquid 10 biologically using biofouling carriers 15, 23, the separation liquid 10 obtained by adding the polymer 6 and separating the solid and the liquid and the digested sludge 5 or returned sludge 20 obtained by the nitrification are mixed, remaining polymer in the separation liquid 10 is removed, and the separation liquid 13 from which the remaining polymer is removed is denitrified biologically using the biofouling carriers 15, 23. For the sludge amount of the sludge to be mixed with the separation liquid 13, 1-10 V% of the separation liquid amount or an amount to be 200-2,000 mg/L- liquid mixture as addition SS is suitable. For the nitrification, a well-known nitrification and denitrification method or a method through nitride nitrogen is usable. <P>COPYRIGHT: (C)2011,JPO&INPIT

Description

  The present invention relates to removal of high-concentration nitrogen contained in digested sludge after anaerobic digestion, and denitrification of separated liquid from digested sludge after anaerobic digestion of organic sludge, sewage sludge, livestock wastewater, etc. The present invention relates to a processing method and apparatus.

Anaerobic digestion of liquid wastes with high organic matter concentrations such as organic sludge and sewage sludge can recover the carbon source, which is organic matter, as methane gas (CH ₄ ) and has a high sludge volume reducing effect. However, in anaerobic digestion, nitrogen in the stock solution is not removed, so the separated liquid during the digested sludge treatment process (including concentrated separation liquid, dehydrated filtrate, digested sludge desorbed liquid, and other waste water from the sludge treatment process) In this case, nitrogen, mainly ammonia nitrogen, remains at a high concentration. In general, a biological nitrification denitrification method is often used as a denitrification treatment for digested sludge separation liquid containing nitrogen at a high concentration. In biological nitrification denitrification, ammonia nitrogen in raw water is oxidized to nitrite nitrogen by ammonia oxidizing bacteria in a nitrification tank, which is an aerobic reaction tank, and nitrite nitrogen is further oxidized by nitrite oxidizing bacteria. Oxidizes to nitrate nitrogen. The treatment liquid from this nitrification tank is introduced into a denitrification tank, which is an anaerobic reaction tank, and the nitrogenous and nitrite nitrogen in the treatment liquid is removed by denitrifying bacteria, which are heterotrophic bacteria. And then reduced to harmless nitrogen gas.

In this biological nitrification denitrification treatment, it is necessary to supply a large amount of oxygen by aeration or the like to maintain an aerobic state in a nitrification tank that oxidizes ammonia nitrogen to nitrate and nitrite nitrogen. In addition, the denitrification tank requires a large amount of organic substances that serve as an electron donor, and if the organic substances are small in the raw water, it is necessary to add methanol. For this reason, there exists a problem which the whole running cost becomes high. In recent years, a denitrification treatment method using an autotrophic denitrifying bacterium that is completely different from a conventional denitrifying mechanism using a heterotrophic denitrifying bacterium has been disclosed (for example, JP-A-2002-361285). A denitrification method in which ammonia nitrogen is used as an electron donor and autotrophic microorganisms using nitrite nitrogen as an electron acceptor are used to react ammonia nitrogen and nitrite nitrogen to convert them into nitrogen gas, This is a method for removing nitrogen by the so-called ANAMOX reaction. With this method, it is not necessary to add organic substances such as methanol to the denitrification tank, and it is not necessary to oxidize the entire amount of ammonia nitrogen in the raw water to nitrite nitrogen and nitrate nitrogen, which greatly increases running costs. Can be reduced. In this method, as shown in the following reaction formula (1), about 1.3 times as much NO ₂ —N reacts with NH ₄ —N 1 and is reduced to nitrogen gas.
^{_{1NH 4 + + 1.32NO 2 - +}} 0.066HCO 3 - + 0.13H +
^{_{→ 1.02N 2 + 0.26NO 3 -.}} + 0.066CH2O 0.5 N0 15 + 2.03H 2 O ··· (1)

On the other hand, the digested sludge after the anaerobic digestion treatment has a high SS of around 20000 mg / L. Therefore, before the nitrogen removal treatment step, concentration separation and dehydration separation are performed, and the separated water after the SS removal and separation is nitrogen. Introduced into the removal process.
A cationic polymer (abbreviated as “polymer” in the present invention) which is a polymer flocculant is used in the concentration and dehydration treatment for separating the digested sludge into a solid and liquid. The polymer addition amount is determined in consideration of digested sludge properties, SS concentration, moisture content of dehydrated cake, and the like. Usually, in order to obtain good treatment performance in the concentration dehydration step, 1.0 to Often 2.0 W%.
The digested sludge properties may vary depending on the properties of sludge charged to the digester, the organic matter concentration, and the like. In the concentration and dehydration step, when the polymer is added in an amount sufficient for agglomeration and stable concentration and dewatering performance is obtained, a polymer often remains in the dehydrated filtrate.

Thus, when a polymer is added to a digested sludge after anaerobic digestion and agglomerated, the separation liquid obtained in the concentration and dehydration step after agglomeration is high in NH ₄ -N and requires a biological denitrification treatment. It becomes. However, if the separation liquid in which the polymer remains is introduced into the nitrification / denitrification step, particularly into a nitrification tank filled with a biological carrier, the nitrification performance becomes extremely unstable and the nitrification rate gradually decreases. It was.
Japanese Patent Laid-Open No. 7-204699 JP 2002-172400 A JP 2002-361285 A

  The present invention solves the above-mentioned problems, and when a separation liquid obtained by adding a polymer to digested sludge and performing solid-liquid separation is denitrified using a biological carrier, high nitrification activity is achieved without reducing the nitrification rate. It is an object of the present invention to provide a method and an apparatus that can be maintained and can perform a stable denitrification treatment.

In order to solve the above problems, in the present invention, in a method of adding a polymer to nitrogen-containing digested sludge for solid-liquid separation, and biologically denitrifying the obtained separated liquid using a bioadhesive carrier, The separation liquid obtained by solid-liquid separation by adding the polymer and the return sludge obtained by the digested sludge or the denitrification treatment are mixed, the residual polymer in the separation liquid is removed, and the residual polymer is removed. A method for denitrification of a digested sludge separation liquid is characterized in that the removed separation liquid is biologically denitrified using a bioadhesive carrier.
In the denitrification apparatus, the amount of sludge mixed with the separation liquid is 1 to 10 V% of the amount of the separation liquid, or the amount of 200 to 2000 mg / L-mixed liquid as added SS is good. In the treatment, a part of the ammonia nitrogen in the separation liquid is converted into nitrite nitrogen, and the resulting nitrite nitrogen and the remaining ammonia nitrogen are denitrified, or the ammonia nitrogen in the separation liquid is removed. Nitrogen can be oxidized to nitrite nitrogen and nitrate nitrogen, and the resulting nitrite and nitrate nitrogen can be denitrified by subordinate denitrifiers in an anaerobic state.

Further, in the present invention, a device for solid-liquid separation of nitrogen-containing digested sludge to which a polymer has been added, and a denitrification device using a bioadhesive carrier for biologically denitrifying the separated liquid obtained by solid-liquid separation In the denitrification treatment apparatus of the digested sludge separation liquid having the above, the separation liquid and the digested sludge or the above for removing residual polymer from the separation liquid obtained by solid-liquid separation in the previous stage of the denitrification apparatus A denitrification treatment apparatus for digested sludge separation liquid is provided, which is provided with a mixing tank for mixing the return sludge obtained from the denitrification apparatus.
In the denitrification apparatus, the solid-liquid separation apparatus may have a concentration separation tank and a dehydrator for obtaining a concentrated separation liquid and a dehydrated filtrate as a separation liquid obtained by solid-liquid separation, and The denitrification apparatus can have a nitrification tank and an ammonia denitrification tank using a bioadhesive carrier, or a nitrification tank, a denitrification tank, and a re-aeration tank.
In the denitrification treatment using the bioadhesive carrier, the bioadhesive carrier and activated sludge may be used in combination.

According to the present invention, the polymer is added to the digested sludge to be agglomerated, and the separated liquid obtained after concentration and dehydration is added and mixed with the digested sludge or the returned sludge obtained from the denitrification process, thereby separating the separated liquid. Residual polymer in the resin is eliminated by agglomeration reaction with SS in the added sludge. Thereby, even if the obtained treatment liquid is introduced into the nitrification process, there is no influence on nitrifying bacteria, and high nitrification activity can be maintained.
In addition, by supplying a part of the digested sludge directly to the mixing tank without concentration and dehydration treatment, the amount of separated liquid supplied to the concentration and dehydration process for solid-liquid separation decreases, so the amount of polymer used can be reduced. This will reduce the chemical cost.

In the present invention, when a polymer is added to the digested sludge and aggregated, the polymer remains in the separated liquid obtained by solid-liquid separation. When the separated liquid is nitrified using a bioadhesive carrier, the nitrification performance is extremely poor. It was made by finding that the nitrification rate is stable and gradually decreases.
FIG. 1 is a graph showing the relationship between nitrification activity and polymer in a batch nitrification test using a nitrification carrier attached with nitrifying bacteria. When the cationic polymer used in the concentrated dewatering of digested sludge remains, the relationship between the nitrification activity ratio after the polymer remains and the polymer residual concentration is shown, assuming that the nitrification activity without polymer residue is 100%.
A decrease in nitrification activity was observed with an increase in the residual polymer concentration. In particular, when the residual polymer was 20 mg / L, the nitrification activity was reduced to 50%, and when the residual polymer was 30 mg / L, the nitrification activity was greatly reduced to 30%.

According to the present invention, a part of the digested sludge is added to the concentrated sludge and dehydrated filtrate (hereinafter separated liquid) obtained in the solid-liquid separation step by concentration and dehydration after adding the polymer to the digested sludge and coagulating. By adding and mixing, the residual polymer in the separation liquid is consumed by agglomeration reaction with the fine SS in the added sludge, and the residual polymer disappears in the separation liquid. Thereby, even if the obtained separated liquid is introduced into a nitrification tank, there is no influence on nitrifying bacteria, and high nitrification activity can be maintained.
In addition, if a part of the returned sludge from the nitrification tank or denitrification tank is mixed with the digested sludge separation liquid in advance, the residual polymer in the separated liquid will coagulate with the returned sludge and there will be no residue in the separated liquid. Even if this mixed solution is introduced into the nitrification tank, there is no influence on nitrifying bacteria, and high nitrification activity can be maintained.

Solid-liquid separation for using a part of the activated sludge in the nitrification tank as a return sludge for removing residual polymer can be generally performed in a sedimentation tank. In addition to a sedimentation basin, a membrane separation method is also possible. In addition to the activated sludge method and activated sludge, the nitrification tank includes a carrier loaded activated sludge method in which a polymer nitrification carrier is filled in the nitrification tank. In any case, according to the present invention, no polymer remains in the inflow raw water, and the nitrifying bacteria activity can be maintained high. In particular, since there is no polymer adhesion on the carrier surface with respect to the carrier charging type nitrification tank capable of maintaining a high concentration of nitrifying bacteria, high nitrification activity can be stably maintained and high nitrification performance can be obtained.
Also for partial nitritation treatment in which a part of NH ₄ —N in the separation liquid is converted to NO ₂ —N, the use of the method of the present invention similarly causes polymer adhesion to the surface of the polymer nitrification carrier. Since the activity of ammonia oxidizing bacteria can be maintained high, stable nitritation treatment performance can be obtained.
A part of the digested sludge is not directly separated into solid and liquid to remove residual polymer, but the amount of digested sludge supplied to the solid / liquid separation process is reduced by mixing directly with the separated liquid. Can be reduced and the chemical cost is reduced.

Furthermore, in the case of the carrier-added activated sludge system that separates solid and liquid in the sedimentation basin, even if the SS of the separation liquid mixed with the digested sludge or return sludge flowing into the nitrification tank is high, it can be settled and separated in the sedimentation basin. Water SS is low. In addition, since a large amount of activated sludge is retained in the nitrification tank, even if some polymer remains temporarily in the influent stock solution, it adheres and aggregates to the activated sludge in the nitrification tank. There is almost no adhesion. As a result, the nitrification rate of the carrier can always be kept high and stable treatment is possible. Further, if clear treated water obtained by settling and separating SS in the settling tank flows into the denitrification tank, the denitrification performance can be stably obtained without being affected by SS and residual polymer.
The presence or absence of polymer residue can be determined by measuring the amount of colloidal charge (unit: meq / L) in the separation liquid. Since the polymer used here is a cationic polymer and has a positive colloidal charge amount, when the colloidal charge amount is 0 or less, it is determined that there is basically no polymer residue. When the colloid charge amount is higher than 0, it can be determined that the polymer remains.

Hereinafter, the present invention will be described in detail with reference to the drawings illustrating an embodiment.
FIG. 2 is a flowchart showing the overall processing flow of the present invention.
In FIG. 2, sewage sludge 4 is anaerobically digested in digestion tank 1, and after adding cationic polymer 6 to digested sludge 5, it is supplied to concentration separation tank 2 and concentrated and separated to obtain separated liquid 7. Then, the sludge concentrate is introduced into the dehydrator 3 to obtain the dehydrated filtrate 8 and the dehydrated cake 9. The concentrated separation liquid 7 and the dehydrated filtrate 8 are combined to form a separation liquid 10 for the treatment according to the present invention.

The separation liquid 10 flows into the mixing tank 11 and a part of the digested sludge 5 from the digester 1 is injected. The injected digested sludge 5 is mixed with the separation liquid 10 by the underwater agitator 12 in the mixing tank 11. A mixed liquid 13 as a separated liquid after mixing is introduced into the nitritation tank 14 as nitritation raw water. In the nitritation tank 14, a part of the inflow NH ₄ -N is oxidized to NO ₂ -N by the action of the nitritation support 15. After the treatment, the mixed liquid in the nitritation tank is separated by the nitritation carrier separation screen 17, the nitritation tank effluent flows into the sedimentation tank 19, and after the sludge sedimentation separation, the supernatant liquid is sublimated. The sludge obtained as the nitrating water 18 and concentrated by sedimentation is returned to the nitritation tank 14 as the return sludge 20. Moreover, the excess sludge 21 is discharged | emitted from a sludge line as needed, and MLSS in the nitritation tank 14 is maintained substantially constant. Nitrite-treated water 18 is introduced into the ammonia denitrification tank 22. In the ammonia denitrification tank 22, NH ₄ -N in the inflow water becomes an electron donor and NO ₂ -N becomes an electron acceptor from the ammonia denitrification bacteria of the denitrification carrier 23, and is denitrified and removed. The denitrification carrier is separated from the mixed liquid after the denitrification removal by the separation screen 17, and the treatment liquid becomes denitrification treated water 24.

The amount of digested sludge added to the mixing tank 11 is sufficient as long as it can coagulate and adsorb the residual polymer in the digested sludge separation liquid. That is, the raw water for biological nitrogen removal, as shown in FIG. 2, the mixed liquid 13 as the nitritation raw water is sampled and analyzed, the colloid charge amount is almost 0 meq / L, and there is no polymer residue. It is desirable to confirm.
In addition, mixing of digested sludge or return sludge and the separated liquid is particularly desirable in order to obtain a sufficient mixing effect in the mixing tank 11 as shown in FIG. 2, and the mixing effect compared to mixing in the mixing tank. Although it is somewhat inferior, it may be performed using other stirring means such as direct mixing by pipe injection.

  In the concentration and dehydration process in which the solid-liquid separation of the digested sludge is performed, in order to achieve stable concentration and dewatering performance, the amount of the cationic polymer added is usually 1.0 to 2.0 W%, that is, 10 to Often 20 mg-polymer / g-SS digested sludge. Most of the added cationic polymer is consumed in the coagulation reaction with the digested sludge, but 5 to 10% of the added polymer remains depending on the digested sludge properties and the coagulation mixing conditions. When the SS of the digested sludge is 20000 mg / L and the polymer addition rate is 1.0 to 2.0 W% with respect to the SS, the amount of polymer added to the digested sludge is 200 to 400 mg / L-digested liquid. If 5 to 10% of the added amount remains, the residual concentration becomes 10 to 40 mg / L-digested liquid. The amount of colloidal charge corresponding to this varies slightly depending on the type of cationic polymer used, but as an example, when the cationic polymer CS-292 is used, it becomes 0.05 to 0.2 meq / L. As described above, it is preferable to appropriately determine the amount of digested sludge to be mixed with the separated polymer residual liquid in accordance with the residual polymer amount. Experiments have shown that if the amount of SS in the digested sludge to be added is 20 to 50 times that of the residual polymer, the polymer can be almost removed.

For example, when the colloid charge amount is 0.05 meq / L and the polymer residual concentration is 10 mg / L, the amount of digested sludge SS to be added is 200 to 500 mg-digested sludge SS / L-mixed solution with respect to the mixed solution. It is desirable. If the digested sludge SS is 20000 mg / L, the added amount of digested sludge is 10 to 25 L per 1 m ³ of the separation liquid to be mixed, and this added amount is 1.0 to 2.5 V with respect to the separated liquid amount. %.
As described above, it is preferable to obtain the residual polymer amount from the colloid charge amount and add the digested sludge amount necessary for removing the residual polymer.
For example, for SS20000mg / L digested sludge, the amount of polymer added is 1W%, which is the lower limit of SS, that is, 200mg / L-digested sludge is added, concentrated and dehydrated, and the treated separation liquid is collected. As a result of measuring the colloidal charge amount according to the sewage test method (1997 version), it was 0.05 meq / L. From the relationship between the polymer charge amount and the concentration, when the polymer residual concentration is calculated to be 10 mg / L, the residual polymer amount is 5% of the added polymer amount, which is considered as the lower limit when the polymer remains. The amount of digested sludge added to the separation liquid is preferably such that the SS increase concentration of the mixed liquid after the addition is 200 to 500 mg / L-mixed liquid.

  Similarly, the concentration of the polymer added is 2 W%, which is the upper limit of SS, that is, 400 mg / L-digested sludge and concentrated dehydration treatment. became. From the relationship between the charge amount and the concentration, when the polymer residual concentration is calculated to be 40 mg / L, the residual polymer amount is 10% of the added polymer amount, which is considered the upper limit when the polymer remains. At this time, if the amount of SS of the digested sludge to be added is 20 to 50 times that of the residual polymer, the amount of digested sludge to be added becomes 800 to 2000 mg / L-mixed liquid with an increased SS concentration of the mixture after the addition. 4 to 10% of the liquid volume. Thus, assuming the lower limit and the upper limit when the polymer remains with respect to the amount of the separation liquid, if the amount of digested sludge added is in the range of about 1 to 10 V%, the polymer remains almost free.

  If the added amount of digested sludge with a high SS is large, the inflow raw water SS becomes high, and in order to retain the nitrifying bacteria of the activated sludge in the nitritation tank, it is necessary to increase the MLSS in the tank. If the MLSS is too high, solid-liquid separation in the sedimentation basin may be difficult. The amount of aeration air for decomposing SS organic matter in the digested sludge is insufficient, which causes a decrease in DO. For this reason, when MLSS in the nitritation tank is 1000 to 5000 mg / L, preferably 2000 to 4000 mg / L, stable treatment is possible. As described above, if the amount of digested sludge added to the mixing tank is 1 to 10 V% or less of the amount of the separated liquid, the mixture SS after digested sludge addition is 200 to 200 when the digested sludge SS is 20000 mg / L. Increased by 2000 mg / L, a sufficient amount. Preferably, if it is 2 to 6 V%, after adding digested sludge, the SS of the mixed solution increases by 400 to 1200 mg / L, and the nitrification tank MLSS does not fluctuate greatly, and the nitrification performance can be stably maintained. Therefore, a higher effect can be obtained.

If a polymer gel carrier capable of adhering and fixing ammonia-oxidizing bacteria is filled in the nitritation tank, the ammonia-oxidizing bacteria can be stably adhered, so that stable nitritation performance can be obtained in the nitritation tank. Gels using synthetic polymers such as polyethylene glycol (PEG), polyvinyl alcohol (PVA), polyacrylamide, and photocurable resin, and polymers such as carrageenan and sodium alginate as the polymer carrier to be filled in the nitritation tank Examples of the carrier include a carrier, polyethylene, polyurethane, and polypropylene.
As the shape of the carrier, any of a spherical shape, a square shape, and a cylindrical shape can be used, and the effective diameter is preferably 3 to 10 mm that can be stably separated from the screen at the outlet of the aeration tank. The specific gravity of the carrier is preferably from 1.001 to 1.05 so that it can flow uniformly in the aerated state. Moreover, it is desirable that the carrier filling amount is 10 to 30 V% which enables uniform mixing flow. It should be noted that the same effect can be obtained even if the above-mentioned carrier is filled in a nitrification tank according to a conventional dependent denitrification system.

Once the nitritation water is introduced into the ammonia denitrification tank via the storage tank, the dissolved oxygen in the nitritation water can be reduced, and a better effect can be obtained.
Also, in the ammonia denitrification tank, if a polymer gel carrier capable of adhering and fixing ammonia denitrifying bacteria is filled, the ammonia denitrifying bacteria can be stably adhered, so that stable denitrification performance can be obtained. Gel carriers using synthetic polymers such as polyvinyl alcohol (PVA), polyethylene glycol (PEG), polyacrylamide, and photocurable resin, and polymers such as carrageenan and sodium alginate as polymer carriers to be filled in the ammonia denitrification tank And fluid carriers made of polyethylene, polyurethane, polypropylene, and the like.
As the shape of the carrier, any of a spherical shape, a square shape, and a cylindrical shape can be used, and the effective diameter is preferably 3 to 10 mm that can be stably separated from the screen at the denitrification tank outlet. A carrier having a large fine pore diameter on the surface, a sponge having a hollow inside, or a material having innumerable irregularities on the surface can quickly attach and fix ammonia denitrifying bacteria, and high denitrification performance can be obtained in a short period of time. Furthermore, since ammonia denitrifying bacteria can be maintained at a high concentration in the denitrification tank for a long period of time, stable denitrification performance can be obtained.
The carrier specific gravity is preferably 1.00 to 1.10, which enables uniform flow by stirring in an anaerobic state. The carrier filling amount is desirably 10 to 30 V% so as not to cause local deposition in the denitrification tank.

Example 1
An example of denitrification treatment according to FIG. 2 is shown below.
Table 1 shows the operating conditions of the mixing tank 11 of FIG. Table 2 shows the processing conditions of the nitritation tank 14 and the ammonia denitrification tank 22.
In the mixing tank 11, a cationic polymer was injected into digested sludge with an SS of 23000 mg / L under the conditions of an injection amount of 350 mg / L, and the separated liquid separated into solid and liquid after the coagulation treatment. Has been introduced. When the colloidal charge amount of this separated liquid was measured and the residual polymer concentration was determined, it was 20 mg / L. For this reason, 5 L / d of the digested sludge is introduced into 250 L / d of this separated liquid, intermittent stirring is performed using an underwater stirrer, and the residual polymer in the separated liquid is added to the fine SS in the digested sludge. Adsorbed and aggregated. The tank mixing SS was around 500 mg / L. When the amount of colloidal charge in the mixed solution after addition and mixing was measured, it was 0 meq / L, and it was confirmed that there was no polymer residue. Incidentally, a mixture of M- alkalinity after mixing, to be about 4 times the _NH 4 -N, advance the mixture _NH 4 -N and M- alkalinity of measures, lack M- alkali The degree was replenished by addition with sodium carbonate.

The nitrite treatment tank was filled with 20 V% of a PEG carrier having an average particle size of 4.2 mm. The mixed solution was continuously passed through the mixing tank at an average of 255 L / d. In the nitritation tank, the pH of the blower was not adjusted, and the output of the blower was adjusted so that DO was around 4 mg / L. Excess sludge was extracted so that the MLSS in the tank was 3000 to 4000 mg / L.
The ammonia denitrification tank was controlled by injecting sulfuric acid so that the pH was 7.9 or less. The denitrification tank was filled with 20 V% of a PVA carrier having an average particle diameter of 4 mm. Further, the nitrous acid treatment water flowing into the ammonia denitrification tank, because the inorganic carbon was little, the Na ₂ CO ₃ as an inorganic carbon source was added 300 mg / L.
Table 3 shows an example of the mixed liquid obtained in Example 1 subjected to continuous water treatment for 6 months and the quality of treated water of each treatment process.

In the nitrification treatment, since the M-alkalinity / NH ₄ -N ratio of the mixed solution was adjusted to 4.0 in advance, about 57% of NH ₄ -N was nitritized and treated water NO ₂ -N Was 440 mg / L, and the NO ₂ —N / NH ₄ —N ratio was 1.29, a value close to the ammonia denitrification theoretical equivalent of 1.32. In the ammonia denitrification treatment, NH ₄ —N and NO ₂ —N of the treated water were 7.8 mg / L and 5.8 mg / L, respectively, and a TN removal rate of 85.9% with respect to the raw water was obtained. In Example 1, the alkaline agent was added directly to the mixing tank in order to replenish the insufficient M-alkalinity in the mixed solution, but a predetermined amount of alkaline agent may be continuously added to the nitritation tank. . The same effect can be obtained by using any one of NaOH, Na ₂ CO ₃ , sodium bicarbonate and the like as the alkali agent added to the mixing tank or nitritation tank.

Example 2
FIG. 3 shows a processing flow used in the second embodiment. The digested sludge separation liquid flowing into the mixing tank 11 was a separation liquid obtained by mixing the separation liquid in the concentration separation tank and the dehydrated filtrate in the dehydration step after aggregation by addition of the polymer as in Example 1.
In Example 2, a part of the return sludge 20 in the nitrification treatment tank is directly added to the mixing tank 11 through the settling tank return line, and the mixture is stirred and mixed with the digested sludge separation liquid. The nitrification tank 14 was supplied. Table 4 shows the processing conditions of the mixing tank in Example 2. The processing conditions for the nitritation tank and the ammonia denitrification tank were the same as in Example 1.

Similar to Example 1, from the measured value of the colloidal charge amount, the residual polymer in the digested sludge separation liquid was estimated to be about 20 mg / L, and the amount of returned sludge mixed in the separation liquid was 20 L / d. The colloid charge amount measured after the addition and mixing was 0 meq / L, and it was confirmed that there was no polymer residue. The MLSS of the returned sludge was 6000 mg / L, and the increased SS after mixing was 430 mg / L. In this case, the return sludge addition amount with respect to the separation liquid amount 260 L / d is 7.7 V%. The separation liquid before the addition and mixing of the returned sludge has an SS of slightly less than 100 mg / L, and the SS in the mixing tank after the addition and mixing is about 500 mg / L. Other conditions are the same as in the first embodiment. The processing conditions for the nitritation tank and the ammonia denitrification tank are the same as those in Example 1.
In Example 2, continuous treatment was performed for about 6 months. As shown in Table 5, the water quality of the nitritation water and the ammonia denitrification water was about the same as in Example 1, and a stable treatment was obtained.

Comparative Example 1
FIG. 4 shows a processing flow of Comparative Example 1 compared with Example 1. The digested sludge separation liquid used here is the same as in Example 1. In Comparative Example 1, a part of the digested sludge and the separation liquid were not mixed, and only the separation liquid was directly supplied to the nitritation tank. Table 6 shows the processing conditions of Comparative Example 1. The NH ₄ —N load in the nitritation tank and the TN load in the ammonia denitrification tank were the same as in Examples 1 and 2. Other conditions were almost the same as in Examples 1 and 2.

Table 7 shows an example of the separated liquid and treated water quality obtained in Comparative Example 1 after about one month from the start of the treatment. Since the polymer was not removed by adding sludge to the same separation liquid as in Examples 1 and 2, the colloidal charge amount of the raw water was 0.2 meq / L, and the polymer remained at about 40 mg / L. As a result, in the nitrite-treated water, NH ₄ -N remained at 470 mg / L, NO ₂ -N remained at 270 mg / L, and NO ₃ -N remained at 15 mg / L. When the polymer residual separation liquid flows into the nitritation treatment tank filled with the carrier, it is considered that the nitrification ability of the carrier is lowered due to the polymer gradually adhering to the carrier. As a result, NH ₄ -N was 130 mg / L higher than Examples 1 and 2, and NO ₂ -N was 170 mg / L lower. Moreover, TN was lower than raw water, and NH ₄ —N stripping was also observed. As a result, NH ₄ —N remains in the ammonia denitrification treated water at 260 mg / L, and the TN removal rate remains at a low value of 59.3%. In addition, the denitrification performance, which is considered to be the effect of free NH ₃ , was lowered due to the residual NH ₄ —N at a high concentration due to long-term continuous treatment. The amount of treated water that can be treated stably decreased gradually, and after about one month from the start of treatment, it became 120 L / d, which was about half or less compared to 255 L / d in Example 1.
Furthermore, in Comparative Example 1, the amount of polymer used for solid-liquid separation of digested sludge was about 1.1 times that of Example 1, resulting in an increase in chemical cost.

Example 3
FIG. 5 shows a process flow in which the present invention is applied to a conventional nitrification / denitrification process using dependent denitrifying bacteria. The separation liquid used here is the same digested sludge separation liquid as in Examples 1 and 2.
Table 8 shows the processing conditions of the mixing tank of Example 3.
In Example 3, as in Example 1, 5 L / d of digested sludge was added to 250 L / d of the separation liquid to remove residual polymer in the separation liquid.

Table 9 shows the nitrification denitrification treatment conditions of Example 3.
The nitrification tank 30 was filled with 20 V% of the same PEG nitrification carrier as in Example 1. Here, the NH ₄ —N load was set to 0.3 kg / m ³ / d. NaOH was injected so that the nitrification tank pH was 7.0. The denitrification tank 33 was filled with 20 V% of the same PVA support as in Example 1. Denitrification is due to the conventional dependent denitrifying bacteria, and methanol was added to the denitrification tank 33. The treated liquid after denitrification was re-aerated in a contact oxidation tank to obtain treated water. In addition, the treated water 38 of the re-aeration tank 37 was circulated to the nitrification tank 30 at twice the amount of inflow water for the purpose of supplying alkalinity to the nitrification tank and diluting the raw water.

Table 10 shows an example of the liquid mixture and water quality of each treatment process obtained in Example 3 carried out for about 6 months as in Examples 1 and 2.

Since the colloidal charge amount of the liquid mixture supplied to the nitrification tank is 0 meq / L and there is no residual polymer, the nitrification performance of the nitrification carrier is good, and the treated water has NH ₄ -N of 0.1 mg / L or less, NO ₃ -N became 260mg / L. In addition, as the nitrification tank treated water, NO ₂ -N may partially remain, but here, it became nitrate type nitrification almost completely. Moreover, in the denitrification tank, as a result of adding methanol about 2.5 times with respect to NO _X -N, the treated water NO ₂ -N was as low as 0.8 mg / L and NO ₃ -N was as low as 2.5 mg / L, The TN removal rate relative to the raw water was 96.9%.

Example 4
FIG. 6 shows another process flow in which the present invention is applied to the conventional nitrification denitrification process. In this embodiment, a mixture of digested sludge mixed with digested sludge is introduced into a nitrification tank 30 filled with a nitrification carrier to perform nitrification, and the treatment liquid from the nitrification tank 30 is used in an activated sludge system. It introduce | transduces into the denitrification tank 33, and subordinate denitrification by methanol addition is performed. The denitrification liquid after the denitrification treatment is subjected to removal of residual methanol and nitrogen gas in the subsequent re-aeration tank 37, and the activated sludge is settled and separated by the sedimentation basin 19 to obtain a supernatant as treated water. On the other hand, the concentrated sludge is returned to the nitrification tank 30 as return sludge 20. Further, a part of the treatment liquid 38 was circulated from the re-aeration tank 37 to the nitrification tank.

As shown in Table 11, the processing conditions of the mixing tank of Example 4 were the same as those of Example 3.
Table 12 shows the nitrification / denitrification treatment conditions of Example 4.
The nitrification tank was a carrier input type activated sludge system, and the load of NH ₄ -N was 0.4 kg / m ³ / d. Further, the TN load of the denitrification tank was also set to 0.4 kg / m ³ / d.

In Example 4 as well, continuous water treatment for about 6 months was performed. The separation liquid and treated water quality during the treatment period were the same as the results of Example 3 shown in Table 10, and stable nitrification / denitrification performance was obtained.

Comparative Example 2
Comparative Example 2 is a comparative example compared to Example 3 in which the present invention is applied to a conventional nitrification denitrification process, and the process flow is shown in FIG. The digested sludge separation liquid used here is the same as in Example 3. A part of the digestive liquid was not mixed with the direct separation liquid, but the separation liquid was directly supplied to the nitrification tank. Other processing conditions were almost the same as in Example 3.
Table 13 shows the separated liquid and treated water quality of Comparative Example 2 after about one month from the start of water flow.
The separation liquid is the same as in Example 3 except SS, and since the polymer is not removed by digestion liquid mixing, the colloid charge amount is as high as 0.2 meq / L, and the residual polymer is 40 mg / L. For this reason, NH ₄ -N was 115 mg / L in the nitrification tank treated water, and remained higher than in Example 3. This is presumably because the residual polymer in the separation liquid adheres to the nitrification carrier in the nitrification tank and the activity of nitrifying bacteria decreases. In the denitrification tank, NO _X -N became approximately 10 mg / L or less by the addition of methanol, but NH ₄ -N remained high. As a result, the TN of the treated water was as high as 145 mg / L, and the removal rate with respect to the separated liquid was only 82.2%.

Example 5
FIG. 7 shows another processing flow when the present invention is applied to the conventional nitrification denitrification system. The processing method is the same as in the fourth embodiment. Here, a part of the returned sludge from the sedimentation basin and the digested sludge separation liquid are added to the mixing tank and mixed with the separation liquid. In this treatment method, the residual polymer in the digested sludge separation liquid is removed, so that the nitrification performance of the nitrification carrier can be stably obtained. Therefore, a high nitrogen removal rate is always obtained.

The graph which shows the relationship between a residual polymer density | concentration and a nitrification support | carrier activity ratio. The flow block diagram which shows an example of the whole processing flow of this invention. FIG. 6 is a flow configuration diagram illustrating a processing flow used in the second embodiment. The flow block diagram which shows the processing flow used for the comparative example 1. FIG. FIG. 9 is a flow configuration diagram showing a processing flow used in the third embodiment. FIG. 9 is a flow configuration diagram showing a processing flow used in Example 4; FIG. 10 is a flow configuration diagram showing a processing flow used in the fifth embodiment. The flow block diagram which shows the processing flow used for the comparative example 2. FIG.

  1: Digestion tank, 2: Concentration separation tank, 3: Dehydrator, 4: Sewage sludge, 5: Digested sludge, 6: Polymer, 7: Concentrated separation liquid, 8: Dehydrated filtrate 8, 9: Dehydrated cakes 9, 10 : Separation liquid, 11: mixing tank, 12: stirrer, 13: mixed liquid, 14: nitritation tank, 15: nitritation carrier, 16: aeration blower, 17: screen, 18: nitrous acid treated water, 19 : Sedimentation basin, 20: return sludge, 21: surplus sludge, 22: ammonia denitrification tank, 23, 35: denitrification carrier, 24, 39: treated water, 25, 34: stirrer, 30: nitrification tank, 31: nitrification carrier 32: Nitrified water, 33: Denitrification tank, 36: Methanol, 37: Re-aeration tank, 38: Circulating water

Claims (8)

In a method for solid-liquid separation by adding a polymer to nitrogen-containing digested sludge and biologically denitrifying the resulting separated liquid using a bioadhesive carrier, the polymer is added to obtain a solid-liquid separation. The separated liquid is mixed with the digested sludge or the return sludge obtained by the denitrification treatment, the residual polymer in the separated liquid is removed, and the separated liquid is removed using a bioadhesive carrier. A method for denitrification of digested sludge separation liquid, characterized by biologically denitrifying treatment. The sludge amount of the sludge mixed with the separated liquid is 1 to 10 V% of the separated liquid amount, or an amount that becomes 200 to 2000 mg / L-mixed liquid as added SS. Denitrification treatment method of digested sludge separation liquid. The denitrification treatment is characterized in that a part of ammonia nitrogen in the separated liquid is converted into nitrite nitrogen, and denitrification treatment is performed from the obtained nitrite nitrogen and the remaining ammonia nitrogen. A method for denitrification of the digested sludge separation liquid according to 1 or 2. The denitrification treatment is characterized in that ammonia nitrogen in the separation liquid is oxidized to nitrite nitrogen and nitrate nitrogen, and the resulting nitrite nitrogen and nitrate nitrogen are denitrified by denitrifying bacteria in an anaerobic state. The method for denitrification of a digested sludge separation liquid according to claim 1 or 2. Digested sludge separation having a device for solid-liquid separation of nitrogen-containing digested sludge added with polymer, and a denitrification device using a bioadhesive carrier for biologically denitrifying the separated liquid obtained by solid-liquid separation In the liquid denitrification treatment apparatus, the first stage of the denitrification apparatus is obtained from the separation liquid and the digested sludge or the denitrification apparatus for removing residual polymer from the separated liquid obtained by solid-liquid separation. A denitrification treatment apparatus for digested sludge separation liquid, characterized in that a mixing tank for mixing the returned sludge is provided. 6. The digested sludge separation according to claim 5, wherein the solid-liquid separation device has a concentration separation tank and a dehydrator for obtaining a concentrated separation liquid and a dehydrated filtrate as a separation liquid obtained by solid-liquid separation, respectively. Liquid denitrification equipment. The denitrification apparatus for digested sludge separation liquid according to claim 5 or 6, wherein the denitrification apparatus has a nitritation tank and an ammonia denitrification tank using a bioadhesive carrier. The denitrification treatment apparatus for digested sludge separation liquid according to claim 5 or 6, wherein the denitrification treatment apparatus has a nitrification tank using a bioadhesive carrier, a denitrification tank, and a re-aeration tank.