JP3772882B2 - Methane fermentation treatment method - Google Patents

Description

  The present invention relates to a methane fermentation treatment that uses anaerobic microorganisms to treat organic waste such as manure, garbage, and food processing residue, and more particularly to a method for treating a fermentation waste liquid that has undergone methane fermentation.

  A method of methane fermentation of organic wastes such as garbage and surplus sludge from sewage and recovering energy as methane gas has been adopted as part of resource saving and recycling society formation.

  Methane fermentation decomposes organic matter into methane and carbon dioxide, but it is not 100% decomposed, and high-concentration organic components remain in the fermentation waste liquid. Further, in the fermentation waste liquid, there is a sludge as a fermentation residue or a microbial cell grown in a methane fermentation tank, and this sludge contains a high concentration of nitrogen components. Furthermore, ammonia, which is a decomposition product of organic matter, is also contained at a high concentration. Therefore, the fermentation waste liquid cannot be discharged into the sewer or river as it is, and a process for decomposing and removing organic substances and nitrogen components is necessary.

  As a method for treating the above methane fermentation waste liquid, an intermittent aeration activated sludge method (hereinafter also referred to as an intermittent aeration method), which is one of activated sludge treatment methods, is known. In this intermittent aeration method, the organic matter in the methane fermentation waste liquid is decomposed and removed as food for microorganisms constituting the activated sludge.

  Nitrogen is aerobic under aeration with air, and ammonia in waste liquid is oxidized to nitrous acid by ammonia oxidizing bacteria, and this nitrous acid is oxidized to nitric acid by nitrite oxidizing bacteria (nitrification reaction). Subsequently, nitrous acid or nitric acid is reduced and removed as nitrogen gas by the action of denitrifying bacteria that oxidize organic matter in the fermentation waste liquid using oxygen in nitrous acid or nitric acid under anaerobic conditions where air aeration is stopped. Nitrogen reaction). Table 1 below summarizes the relationship between nitrogen removal and microorganisms.

  In order to efficiently perform such intermittent aeration processing, for example, in Patent Document 1 below, the pH change in the reaction tank in which intermittent aeration processing is performed is measured, and the end of the nitrification reaction is detected from the inflection point. In addition, a nitrogen-containing wastewater treatment method is disclosed in which the raw water nitrogen concentration is estimated from the obtained nitrification time, and the raw water flow rate is controlled in order to make the nitrogen load of the reaction tank constant from the raw water nitrogen concentration.

  Furthermore, in the following Patent Document 2, in the intermittent aeration treatment method in which aerobic treatment and anaerobic treatment are repeated in a single reaction tank, the ratio of aerobic time and anaerobic time is set based on the temperature and pH in the reaction tank. A method of controlling is disclosed.

Furthermore, in Patent Document 3 below, when performing denitrification treatment of organic wastewater by the intermittent aeration activated sludge method, the treated water pH is sequentially stored in the storage means, and the time-dependent change in the stored pH value is described. Based on the presence or absence of the occurrence of a point at which the pH change rate reaches zero after the pH change rate reaches the standard rate by causing the calculation means to calculate the pH change rate and the pH change width in each aerobic microorganism treatment and anaerobic microorganism treatment, Diagnosing the progress of nitrification and denitrification reactions is disclosed.
Japanese Patent Laid-Open No. 11-253990 JP-A-10-249386 JP-A-8-323394

  As described above, the intermittent aeration method uses the organic matter in the wastewater to reduce nitrous acid or nitric acid into nitrogen gas, and therefore requires an amount of organic matter commensurate with the amount of nitrogen.

  However, in methane fermentation, the amount of organic matter required for the denitrification step tends to be insufficient because the organic matter is decomposed in the fermentation waste liquid during the methane fermentation process. For this reason, there has been a problem that it is necessary to add methyl alcohol or the like as an organic substance source. In addition, there is a problem in that aeration power is required when performing air aeration in order to advance the nitrification reaction, and the aeration power for supplying the air is required, which increases costs.

  In the above Patent Documents 1 to 3, although the end of the aerobic reaction is detected by the pH change in the reaction tank, the time and temperature of air aeration are optimally controlled using this detection, The amount of organic substances necessary for denitrification during an anaerobic reaction and the amount of aerated air during an aerobic reaction have not been studied.

  The object of the present invention was made in view of the above-mentioned problems of the prior art, and by controlling the nitrification reaction in the intermittent aeration tank with a nitrite type, the amount of air required in the nitrification process can be reduced, Furthermore, it is providing the method which can reduce the organic substance required amount in a denitrification process.

That is, in the methane fermentation treatment method of the present invention, an organic waste is put into a methane fermentation tank, methane-fermented by anaerobic microorganisms and taken out as a fermentation waste liquid, and then this fermentation waste liquid is put into an activated sludge tank. An intermittent aeration process in which air aeration and aeration stop are alternately repeated, and the ammonia in the fermentation waste liquid is converted to nitrogen gas to be removed, and a methane fermentation treatment method,
The air aeration is performed at 25 to 35 ° C., and at the air aeration, at least one selected from pH, dissolved oxygen, and ammonia concentration in the activated sludge tank is measured, whereby ammonia nitrogen is converted into nitrite. The time for completing the reaction for conversion to nitrogen is detected for each cycle in which the air aeration and the aeration stop are alternately repeated, and the air aeration time is 1 to 1.5 times the detected end time . It is characterized by controlling to become .

  Generally, ammonia nitrification reaction and denitrification reaction proceed according to the following formulas (1) to (4). Among these, the expressions (1) and (2) are aerobic reactions (nitrification reaction) in air aeration, and the expressions (3) and (4) are anaerobic reactions (denitrification reaction) when aeration is stopped.

NH ₄ ⁺ + 3 / 2O ₂ → NO ₂ ⁻ + H ₂ O (1)
^{_{NO 2 - + 1 / 2O 2}} → NO 3 - ·············· (2)
^{_{2NO 2 - + 6H → N 2}} + 2H 2 O + 2OH - ······· (3)
^{_{2NO 3 - + 10H → N 2}} + 4H 2 O + 2OH - ······ (4)
In this invention, the said air aeration is performed at 25-35 degreeC. The growth rate of ammonia-oxidizing bacteria and nitrite-oxidizing bacteria is temperature-dependent. Under temperature conditions of about 15 ° C or higher, the growth rate of ammonia-oxidizing bacteria is faster than that of nitrite-oxidizing bacteria. The difference is known to increase. Therefore, by performing air aeration at 25 to 35 ° C., only nitrite-oxidizing bacteria are reduced in the nitrification reaction, the reaction from nitrous acid to nitric acid does not proceed, and the nitrification reaction to nitrous acid is performed in a short time. You can stop at.
In the present invention, in the air aeration, the reaction for converting ammonia nitrogen into nitrite nitrogen by measuring at least one selected from pH, dissolved oxygen, and ammonia concentration in the activated sludge tank. Is detected for each cycle in which the air aeration and the aeration stop are alternately repeated, and the air aeration time is controlled to be 1 to 1.5 times the detected end time. To do. The ratio of the growth rate of ammonia-oxidizing bacteria / nitrite-oxidizing bacteria is about 1.5 under relatively high temperature conditions. Therefore, nitrite-oxidizing bacteria cannot be maintained in the system by minimizing the time required for air aeration to complete the reaction for converting ammoniacal nitrogen to nitrite nitrogen and maximizing this 1.5 times. Can be with conditions.
Thus, according to the method of the present invention, the time and temperature of air aeration were adjusted so that the number of ammonia oxidizing bacteria in the activated sludge tank increased and the number of nitrite oxidizing bacteria decreased. Therefore, in the nitrification reaction among the above reactions, only the reaction of the formula (1) for converting ammonia nitrogen to the nitrite nitrogen proceeds, stops at the nitrous acid, and the reaction of the formula (2) does not proceed. Therefore, since the oxygen content of the formula (2) is not necessary, the oxygen amount (air amount) necessary for air aeration can be reduced by up to 25%.

  As a result, in the denitrification reaction, the reaction (4) denitrifying from nitric acid does not proceed, and only the denitrification from nitrous acid (3) proceeds. Here, when the formula (3) is compared with the formula (4), the formula (3) requires 40% less hydrogen. Since this hydrogen is obtained from an organic substance supplied into the system, denitrification from nitrous acid of the formula (3) can be performed with a smaller amount of organic substance. Therefore, the amount of organic matter necessary for denitrification can be reduced, and the addition of methanol at the time of denitrification is not required, or the amount of methanol added can be reduced.

In the present invention, the time for completing the reaction for converting the ammonia nitrogen to the nitrite nitrogen is measured by measuring at least one selected from pH, dissolved oxygen, and ammonia concentration in the activated sludge tank. determined by.

End point of the upper Symbol of formula (1), can be detected in the presence of ammonium ions, pH, dissolved oxygen, by at least one selected from ammonia concentration, reaction of converting the ammonium nitrogen to nitrite nitrogen The end time can be easily detected.

  Furthermore, in the present invention, an upper limit value and a lower limit value of the air aeration time are set in advance, and the time for completing the reaction for converting the ammonia nitrogen to the nitrite nitrogen is the upper limit value or the lower limit value. The air aeration is preferably terminated when the value is exceeded.

  According to this aspect, the upper limit value is set so that, for example, the time for completing the denitrification is calculated in advance in the anaerobic time from the operating temperature, nitrogen load, and denitrification speed, and that time can be secured in one cycle. . The lower limit value is set in advance by calculating the required aerobic time under the operating temperature conditions from the growth rate of ammonia oxidizing bacteria such as literature values. As a result, the intermittent aeration process can be completed within one cycle.

  Moreover, in this invention, it is preferable that the cycle which repeats the said air aeration and aeration stop alternately is 1-4 hours. According to this aspect, by setting one cycle to 1 hour or longer, it is possible to prevent erroneous detection of the time when the reaction from ammonia to nitrous acid ends. That is, when one cycle is short, the amount of raw water entering the day is reduced, and the concentration fluctuations of aerobic and anaerobic ammonia and nitrous acid are reduced, making it difficult to grasp the end point, but this can be prevented. Further, by setting one cycle to 4 hours or less, the concentration fluctuations of ammonia and nitrous acid are increased, and it is possible to prevent the ammonia and nitrous acid concentrations from becoming too high and inhibiting the nitrification reaction.

  According to the present invention, the nitrification reaction in the intermittent aeration tank can be controlled by the nitrite type, whereby the amount of air required in the nitrification step can be reduced and the cost required for aeration can be reduced. Further, since the required amount of organic substances in the denitrification process can be reduced, it is unnecessary to add methyl alcohol or the like as an organic substance source, or the addition amount can be reduced, and the cost of the denitrification process can be reduced.

  Hereinafter, the present invention will be described in more detail with reference to the drawings. FIG. 1 shows a schematic configuration diagram of an embodiment of a methane fermentation treatment apparatus used in the method of the present invention.

  The processing apparatus of FIG. 1 is mainly comprised from the methane fermentation tank 1 and the intermittent aeration tank 3 for processing the fermentation waste liquid after methane fermentation. And the piping from the methane fermentation tank 1 is connected to the intermittent aeration tank 3 via the supply pump 2, and the intermittent aeration tank 3 is connected to a pipe for discharging treated water.

  An aeration device 7 is provided at the bottom of the intermittent aeration tank 3 so that the fermentation waste liquid can be aerated with a gas containing oxygen (normal air). A conventionally well-known thing can be used as the aeration apparatus 7, and it is not specifically limited. On the other hand, the stirrer 5 is provided in the upper part in the intermittent aeration tank 3, and the fermentation waste liquid can be stirred by the stirring blade. A conventionally well-known thing can be used also as the stirrer 5, and it is not specifically limited.

  A thermometer 4 is connected to the upper part of the intermittent aeration tank 3, and a temperature adjustment device 8 is provided so as to adjust the temperature in the intermittent aeration tank 3 based on the measured value. As the temperature control device 8, a conventionally known heater or the like can be used.

  In addition, a pH meter is connected to the upper part of the intermittent aeration tank 3, and the aeration time can be determined by monitoring the pH in the fermentation waste liquid by a method described later.

  Next, the methane fermentation treatment method of the present invention using this processing apparatus will be described. In FIG. 1, organic waste such as livestock manure such as cattle and pigs and garbage is crushed and crushed in advance. According to the above, the slurry is diluted with an appropriate amount of water to form a slurry, and then charged into the methane fermentation tank 1.

  In the methane fermenter 1, slurry methane fermentation is performed, and organic waste is decomposed by anaerobic microorganisms. Although the methane fermentation temperature is not particularly limited, for example, it can be performed at 50 to 60 ° C. According to this, since the fermentation with a high-temperature methane bacterium having higher activity can be performed, the decomposition rate of the organic waste can be further improved. Then, the same amount of fermented liquid as the slurry supplied at regular time intervals is extracted from the methane fermentation tank 1 by the supply pump 2 and sent to the intermittent aeration tank 3. The biogas generated in the methane fermentation tank 1 is collected in a gas holder (not shown) and is effectively used as a fuel for a power generator such as a fuel cell power generation device or a gas engine or a boiler.

  Next, in the intermittent aeration tank 3, the intermittent aeration process by the activated sludge method is performed. That is, first, air as aeration gas is supplied by the aeration apparatus 7 and the above nitrification reaction is performed under aerobic conditions.

  At this time, in the present invention, in air aeration, the time and temperature of air aeration are set so that the number of ammonia oxidizing bacteria in the intermittent aeration tank 3 increases and the number of nitrite oxidizing bacteria decreases. It is characterized by adjusting.

  As described above, air aeration is performed by the following formula (1) for converting ammonia nitrogen to nitrite nitrogen by ammonia oxidizing bacteria, and the following formula (1) for converting the nitrite nitrogen to nitrate nitrogen by nitrite oxidizing bacteria ( 2) It proceeds by an oxidation reaction consisting of the formula:

NH ₄ ⁺ + 3 / 2O ₂ → NO ₂ ⁻ + H ₂ O (1)
^{_{NO 2 - + 1 / 2O 2}} → NO 3 - ············ (2)
Microorganisms related to the nitrification reaction are ammonia oxidizing bacteria and nitrite oxidizing bacteria. There is a difference in the growth rate of ammonia-oxidizing bacteria and nitrite-oxidizing bacteria. Under temperature conditions of about 15 ° C or higher, the growth rate of ammonia-oxidizing bacteria is faster than that of nitrite-oxidizing bacteria. (LGJMvan Dongen, MSMJetten, MCMvan Loosdrecht, The Combined Sharon / Anammox Process, STOWA Report, IWA Publishing, 2001, p8).

  Therefore, if each bacterium flows out of the intermittent aeration tank earlier than the speed at which ammonia-oxidizing bacteria grow and faster than the speed at which nitrite-oxidizing bacteria grow, only the nitrite-oxidizing bacteria will decrease and The reaction to nitric acid will not proceed, and the nitrification reaction will stop at nitrous acid.

  Therefore, in the present invention, air aeration is preferably performed at a temperature at which the growth rate of ammonia-oxidizing bacteria is higher than the growth rate of the nitrite-oxidizing bacteria. Specifically, the temperature is measured by the thermometer 4, It is more preferable to perform air aeration while controlling to 25-35 degreeC using the temperature control apparatus 8. FIG.

  If the temperature is less than 25 ° C., the difference in growth rate between the ammonia-oxidizing bacteria and the nitrite-oxidizing bacteria is small, and a stable operation cannot be performed. On the other hand, if the temperature exceeds 35 ° C., the activity of the bacteria is lowered and the treatment efficiency is lowered, which is not preferable.

  In the present invention, the air aeration time is preferably 1 to 1.5 times as long as the reaction time for converting the ammoniacal nitrogen to the nitrite nitrogen is completed.

  The intermittent aeration method in the present invention removes nitrogen by repeatedly performing an aerobic condition and an anaerobic condition. However, the above microorganisms that oxidize ammonia and nitrous acid can grow under an aerobic condition. In anaerobic conditions, it cannot grow and only kills. Here, the growth rate of the ammonia-oxidizing bacteria that oxidize ammonia can be considered to be almost constant without depending on the ammonia concentration in the system, so under the conditions where the intermittent aeration tank is stably operated, The time required for the end of the aerobic ammonia oxidation (the time until the ammonia concentration is reduced to zero) is the minimum time required for maintaining the bacteria in the system against the ammonia oxidizing bacteria.

  On the other hand, since the growth rate of nitrite-oxidizing bacteria is slower than that of ammonia-oxidizing bacteria as described above, the amount of death and outflow to the outside of the system can be reduced by operating only at the aerobic time necessary for the growth of ammonia-oxidizing bacteria. In order to win, nitrite-oxidizing bacteria cannot be maintained in the system, and as a result, the oxidation of ammonia stops up to nitrite.

  When air aeration is performed in less than the time (less than 1 time) when the reaction for converting ammonia nitrogen to nitrite nitrogen is completed (less than 1 time), the ammonia-oxidizing bacteria are more likely to die and outflow out of the system. Therefore, ammonia-oxidizing bacteria gradually decrease, which is not preferable because ammonia oxidation does not proceed.

  The ratio of the growth rate of ammonia-oxidizing bacterium / nitrite-oxidizing bacterium is about 1.5 at maximum under the condition of relatively high temperature as described above. Therefore, by setting the time of air aeration to 1.5 times or less of the time for completing the reaction for converting ammonia nitrogen to nitrite nitrogen, the condition that nitrite oxidizing bacteria cannot be maintained in the system is set. Can do. On the other hand, if it exceeds 1.5 times, it becomes a condition that nitrite oxidizing bacteria can also grow, and the reaction from nitrous acid to nitric acid proceeds, which is not preferable.

  In this embodiment, the pH meter 6 is used to measure and determine the time for completing the reaction for converting ammoniacal nitrogen to the nitrite nitrogen.

  In the intermittent aeration tank 3, the pH decreases as the nitrification reaction proceeds under aerobic conditions. When ammonia is exhausted, the pH stops decreasing, and then the carbon dioxide gas is degassed, so the pH tends to increase. Indicates. Therefore, the end of the above equation (1) can be determined from the inflection point of the pH.

  FIG. 2 is an example of a control block diagram for detecting the time at which the reaction of converting ammonia nitrogen into the nitrite nitrogen is completed from the above-described pH inflection point.

  First, after removing noise (step S2) from the signal from the pH meter 6 (step S1) using a first-order lag filter, a differentiation operation is performed using a differentiator (step S3). Since the differential value changes from minus to plus at the point where ammonia disappears (step S4), the time when this change occurs is detected as Ta (step S5). The value obtained by multiplying Ta by 1 to 1.5 is defined as T (pH) (step S6), and the elapsed time (T) and T (pH) in the aerobic condition are compared (step S7), and T> T (pH ), The aeration apparatus 8 is stopped (step S8), and the aerobic condition is completed.

  FIG. 3 is another example of a control block diagram for detecting the time at which the reaction of converting ammonia nitrogen into the nitrite nitrogen is completed from the above-described pH inflection point. This example differs from FIG. 2 in that instead of detecting differential points as in S3 and S4 above, pH difference calculation is performed in S9 and S10, and change points are detected depending on whether the difference is positive or negative. ing.

  That is, after the signal from the pH meter 6 (step S1) is denoised by a first-order lag filter (step S2), this value is temporarily stored in the memory (step S9). Thereafter, a difference is calculated by comparison with a value after a predetermined time, for example, 60 to 180 seconds (step S10).

  For example, if difference = (current pH) − (memory stored value), when this difference is negative, the nitrification process of the aerobic process where the pH is decreasing is in progress, and when the difference is positive, the pH is Since it is rising, the nitrification process is complete. Therefore, the change point at which this difference turns from negative to positive is determined (step S11), and the time at which this change point occurs may be detected as Ta (step S5). A value obtained by multiplying 1 to 1.5 is set to T (pH) (step S6), the elapsed time (T) of aerobic conditions is compared with T (pH) (step S7), and T> T (pH) At that time, the aeration apparatus 8 may be stopped (step S8), and the aerobic condition may be completed.

  Note that an upper limit and a lower limit are set in advance for this aerobic time, and when the T (pH) is outside the range of the upper and lower limits, the aerobic time is terminated at the upper limit or the lower limit. Is preferred.

  As the upper limit value, for example, the time for completing the denitrification in the anaerobic time is calculated from the operating temperature, the nitrogen load, and the denitrification speed, and is set so that the time can be secured in one cycle. Further, as the lower limit value, the necessary air aeration time under the operating temperature condition is calculated and set from the growth rate of ammonia oxidizing bacteria such as literature values.

  After the air aeration is completed, the stirrer 5 is moved, and a certain amount of fermentation waste liquid is supplied from the supply pump 2. In this state, the intermittent aeration tank 3 is in a state where there is no dissolved oxygen, and denitrification reaction from nitrous acid, which is the reaction of the above formula (3), proceeds. At this time, since nitric acid is generated in the aerobic reaction, the reaction of the above formula (4) in the denitrification reaction does not proceed, and as a result, only the reactions of the above formulas (1) and (3) are performed. It progresses predominantly and becomes a state where nitric acid is not generated.

  The total of the aerobic time and the anaerobic time is preferably set to 1 to 4 hours by a timer or the like. As a result, in this embodiment, the difference between the cycle time and the air aeration time obtained by the above method is the time for the anaerobic condition.

  FIG. 4 shows a schematic configuration diagram of another embodiment of the methane fermentation treatment apparatus that can be used in the method of the present invention. In the following description of the embodiment, the same parts as those in the above embodiment are given the same reference numerals, and the description thereof is omitted.

  This embodiment is different from the above embodiment only in that a dissolved oxygen meter 9 is used instead of the pH meter 6 in the above embodiment.

  In this case, first, the aeration apparatus 7 is controlled so that the dissolved oxygen concentration by the dissolved oxygen meter (DO meter) 9 is 0.5 to 2 mg / L. And in the state where ammonia remains in the intermittent aeration tank 3, the consumption of oxygen due to ammonia oxidation is large, but when the ammonia is exhausted, the oxygen consumption is rapidly reduced and the detection value of the dissolved oxygen meter 9 is rapidly increased. By detecting this increase, the end of the expression (1) can be determined. Thus, in this invention, you may determine completion | finish of said (1) Formula by measuring a dissolved oxygen concentration.

  FIG. 5 shows a schematic configuration diagram of still another embodiment of the methane fermentation treatment apparatus that can be used in the method of the present invention. In this embodiment, only the point that the ammonia meter 10 is used instead of the pH meter 6 in the first embodiment is different from the first embodiment.

  In this case, by measuring the ammonia concentration in the intermittent aeration tank 3 with the ammonia meter 10 and detecting the time until the ammonia concentration becomes zero, the end of the equation (1) can be determined. Thus, in the present invention, the end of the above equation (1) may be determined by directly measuring the ammonia concentration.

  Using the apparatus configured as shown in FIG. 1, the fermentation waste liquid after the methane fermentation treatment was treated in the intermittent aeration tank 3. The result is shown in FIG. FIG. 6A is a graph obtained by determining changes with time of various nitrogen compounds during intermittent aeration treatment, and FIG. 6B is a graph showing changes in pH at that time.

  First, the aeration apparatus 7 was operated. As a result, as shown in FIG. 6 (b), when the aerobic process was started, the pH in the intermittent aeration tank 3 gradually decreased due to the nitrification reaction, and became an inflection point after 40 minutes and started to rise. . This pH change point is detected, and the aeration apparatus 7 is operated up to 60 minutes based on the detection time and then stopped. Then, while the agitator 5 is moved, a constant amount of methane fermentation liquid is intermittently supplied by the supply pump 2. 3 was supplied. In addition, the control method of FIG. 3 was used for detection of the change point of pH.

As a result, as shown in FIG. 6A, the ammonia concentration (NH ₄ -N) in the intermittent aeration tank gradually decreases and becomes zero after 40 minutes. On the contrary, the nitrite concentration (NO ₂ -N) became constant after 40 minutes. Thereafter, in an anaerobic state after 60 minutes, the ammonia concentration increased again and the nitrous acid concentration gradually decreased.

Since the nitric acid concentration (NO ₃ -N) at this time was always almost zero, only the formulas (1) and (3) proceed in the above-described ammonia nitrification reaction and denitrification reaction. It can be seen that the formulas (2) and (4) that generate nitric acid do not proceed.

  The methane fermentation treatment method of the present invention is suitably used for treating organic waste such as manure, raw garbage, and food processing residue.

It is a schematic block diagram which shows one Embodiment of the methane fermentation processing apparatus used for this invention. It is an example of the control block diagram which detects the inflection point of pH during an intermittent aeration process. It is another example of the control block diagram which detects the inflection point of pH during intermittent aeration processing. It is a schematic block diagram which shows other embodiment of the methane fermentation processing apparatus used for this invention. It is a schematic block diagram which shows other embodiment of the methane fermentation processing apparatus used for this invention. It is the graph which calculated | required the time-dependent change of various nitrogen compounds and pH during an intermittent aeration process.

Explanation of symbols

DESCRIPTION OF SYMBOLS 1 Methane fermentation tank 2 Supply pump 3 Intermittent aeration tank 4 Thermometer 5 Stirrer 6 pH meter 7 Aeration apparatus 8 Temperature control apparatus 9 Dissolved oxygen meter 10 Ammonia meter

Claims (2)

An organic waste is put into a methane fermentation tank, methane-fermented with anaerobic microorganisms and taken out as a fermentation waste liquid, and then this fermentation waste liquid is put into an activated sludge tank to intermittently repeat air aeration and aeration stop alternately. A methane fermentation treatment method in which aeration treatment is performed and ammonia in the fermentation waste liquid is converted to nitrogen gas and removed.
The air aeration is performed at 25 to 35 ° C., and at the air aeration, at least one selected from pH, dissolved oxygen, and ammonia concentration in the activated sludge tank is measured, whereby ammonia nitrogen is converted into nitrite. The time for completing the reaction for conversion to nitrogen is detected for each cycle in which the air aeration and the aeration stop are alternately repeated, and the air aeration time is 1 to 1.5 times the detected end time . The methane fermentation processing method characterized by controlling so that it may become . The methane fermentation treatment method according to claim 1, wherein the air aeration and cycle repeating aeration stop and the alternately 1 to 4 hours.

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