JP5049748B2 - Biological water treatment simulation method and simulation apparatus - Google Patents

Description

  The present invention relates to a biological water treatment simulation method and a simulation apparatus. More particularly, the present invention relates to a biological water treatment simulation method and a simulation apparatus useful for biological water treatment.

  Currently, in water treatment, for example, sewage treatment, factory wastewater treatment, etc., processing efficiency, advancement of treatment capacity, energy saving of energy used for water treatment, reduction of cost of water treatment, etc. are being promoted. Yes. For example, based on experience, it is difficult to predict process behavior under various conditions and to set the operating conditions of a water treatment facility. Therefore, there is a drawback that water treatment is inefficient, resulting in waste of energy and an increase in cost. For this reason, instead of predicting the behavior of processes under various conditions based on experience, simulations have been introduced to calculate reactions such as bacterial growth and death, and attempts have been made to make more quantitative predictions. (For example, refer to Patent Documents 1 to 4).

  In Patent Document 1, a reaction model matrix of substances involved in a reaction process of treatment using a circulation nitrification denitrification method, a kinetic model of a treatment state based on a reaction rate equation, a reaction rate constant, and each coefficient value. And a water quality simulation apparatus of a circulation type nitrification denitrification method for obtaining an output for controlling the operation of a plant from the result. In the invention described in Patent Document 1, soluble BOD, nitrate nitrogen, ammonia nitrogen, BOD assimilating bacteria, nitrifying bacteria, dissolved oxygen, and alkalinity are used as target substances of the kinetic model. . However, in the invention described in the cited document 1, many kinds of microorganisms having denitrification ability are combined into one kind of microorganism (BOD assimilating bacteria), and one kind of microorganism (nitrifying bacteria) is also provided for microorganisms having nitrification ability. ) Occurs in the type of bacteria, the number of bacteria, the ability to decompose bacteria (specifically, oxidation and reduction ability), and the decomposition process (specifically, nitrification and denitrification processes) Nitrous acid has a drawback that it is not reflected in the simulation.

  Patent Document 2 discloses an IAWQ (currently “IWA”) activated sludge model No. which models a unit device constituting a sewage treatment process as a part. 2 and IAWQ (currently “IWA”) activated sludge model no. 2 includes a simulator for obtaining a model component output value for each part based on the model component input value, a measuring means for measuring the quality of the inflow water flowing into the sewage treatment process online, and the measurement value and the model component input value. There is disclosed a sewage treatment process simulator system that includes a conversion unit that uses a correlation equation and includes a calculation unit that converts a measurement value from the measurement unit into a model component input value using the correlation equation of the conversion unit. However, although the invention described in Patent Document 2 calibrates the reaction kinetic constant based on the quality of the influent water and the treated water, the nitrification / denitrification process can be performed even when the same treatment facility is targeted. May not be reproducible.

  Further, in Patent Document 3, a mixture of organic waste water and activated sludge is aerated in an aeration tank, and the dissolved oxygen concentration in the aeration tank is based on the detected value of the dissolved oxygen concentration control element and the deviation of the set value. In the controlled water treatment system, kinetic constants when the treated water is stable, carbon and nitrogen substrate removal rate equations, carbon and nitrogen cell growth rate equations, substances related to dissolved oxygen concentration A numerical simulation was performed using the balance equation and the material balance equation for the amount of sludge in the process, thereby obtaining time-dependent data on the amount of nitrified bacteria in the process or the nitrification rate in the steady state. A first simulator unit that outputs a value with a stable quantity or nitrification rate as a target value, and the kinetic constant is expressed as a function of an environmental factor, and a kinetic constant corresponding to the environmental factor at each time point is used. Both of the above-mentioned target values are introduced and a simulation by numerical calculation is performed using the above-described equations, thereby providing a second simulator section for obtaining an optimum set value of the dissolved oxygen concentration control element at each time point. An apparatus is disclosed. In the invention described in the cited document 3, the time-dependent data of the amount of nitrifying cells or the nitrification rate is obtained by simulation, and a value in which the amount of nitrifying cells or the nitrification rate is stable is set as a target value among the time-dependent data. Then, an optimum dissolved oxygen set value is obtained from the time series data of the target value and kinetic constant, and the dissolved oxygen concentration is controlled based on the dissolved oxygen set value and the actually measured dissolved oxygen concentration value. However, the invention described in Patent Document 3 has a drawback that the quality of treated water cannot be predicted.

Furthermore, in Patent Document 4, the substrate intake behavior, growth behavior, and death behavior of nitrifying bacteria involved in the nitrification reaction are ruled based on the relationship between oxygen in the vicinity of the bacteria and the existence state of the substrate, and the nitrifying bacteria are placed in a virtual region. , Substrate, and oxygen are set based on the concentration of nitrifying bacteria, oxygen concentration and substrate concentration, and the behavior of each nitrifying bacteria set is calculated according to the rules. A nitrification reaction simulation method for obtaining at least one of the number, the presence state of oxygen, and the presence state of a substrate is disclosed. However, in the invention described in Patent Document 4, the nitrification reaction is only simulated, and the number of nitrifying bacteria, the oxygen concentration, and the substrate concentration can be obtained, but there is a drawback that the quality of treated water cannot be predicted. Further, the invention described in Patent Document 4 has a drawback that it cannot be sufficiently reflected in the simulation when factors other than the number of nitrifying bacteria, oxygen concentration and substrate concentration affect the treatment.
JP-A-8-323393 JP 2000-107796 A Japanese Examined Patent Publication No. 7-106357 JP 9-47785 A

  The present invention can reflect the fluctuation of the number of bacteria of various microorganisms contained in the activated sludge, a series of resolution fluctuations by the microorganisms, and the like, and can simulate the behavior of the water treatment process and the treated water quality with higher accuracy. Another object is to provide a biological water treatment simulation method. In addition, the present invention reflects the fluctuations in the number of various microorganisms contained in the activated sludge and the variation in the resolution due to the microorganisms, and simulates the behavior of the water treatment process and the treated water quality with higher accuracy. Another object is to provide a biological water treatment simulation apparatus capable of performing the above-described problems.

（式中、ηは活性パラメータ、μmaxは最大比増殖速度［ｈｒ-1］であり、Ｃは基質濃度、Ｋは飽和定数であり、ｎは反応に関与する基質の数であり、Ｘ（Ｃｅｌｌ）は細菌数から求められた細菌の濃度［ｍｇ−ＣＯＤ／ｌ］を示す。）

（式中、ηは活性パラメータ、μmaxは最大比増殖速度［ｈｒ-1］であり、Ｃは基質濃度であり、Ｋは飽和定数であり、ｎは反応に関与する基質の数であり、Ｘ（Ｃｅｌｌ）は細菌数から求められた細菌の濃度［ｍｇ−ＣＯＤ／ｌ］であり、Ｐは反応阻害物質の濃度であり、ｍは、反応阻害物質の数を示す。）
〔２〕（Ａ）活性汚泥に含まれ、かつ該被処理水中の処理対象物質の分解に関与する細菌の種類毎の細菌数を遺伝子解析法により決定する工程、
（Ｂ）前記工程（１）で決定された細菌の種類毎の細菌数から、遺伝子解析に基づく細菌濃度を算出する工程、
（Ｃ）前記活性汚泥における処理対象物質の分解速度から活性を測定する工程、
（Ｄ）前記工程（Ｂ）で算出された細菌濃度と、前記工程（Ｃ）で算出された活性とから活性パラメータを算出する工程、および
（Ｅ）前記工程（Ｄ）で算出された活性パラメータと、水処理プロセスの条件成分値と、対象となる生物反応槽の仕様と、生物反応槽の運転条件と、前記工程（Ａ）で決定された細菌の種類毎の細菌数とに基づき、活性汚泥モデルにより、処理水質をシミュレーションする工程、
を含む、請求項１記載の生物学的水処理のシミュレーション方法。
〔３〕 該活性汚泥モデルが、ＩＷＡ活性汚泥モデルＮＯ．３（ＡＳＭ３）に基づいて改良されたものである、前記〔１〕または〔２〕記載の生物学的水処理のシミュレーション方法、
〔４〕 該遺伝子解析法が、リアルタイムＰＣＲである、前記〔１〕〜〔３〕いずれか１項に記載の生物学的水処理のシミュレーション方法、
〔５〕 該処理対象物質の分解に関与する細菌が、該処理対象物質の分解に関与して酸化能力を発揮する細菌および／または該処理対象物質の分解に関与して還元能力を発揮する細菌であり、該細菌に対応して、処理対象物質の分解に関与する活性が、該処理対象物質の分解に関与する酸化活性および／または該処理対象物質の分解に関与する還元活性である、前記〔１〕〜〔４〕いずれか１項に記載の生物学的水処理のシミュレーション方法、
〔６〕 該酸化活性として、アンモニア酸化活性と亜硝酸酸化活性とを含む硝化活性を測定し、かつ該還元活性として、硝酸還元活性と亜硝酸還元活性とを含む脱窒活性を測定する、前記〔５〕記載の生物学的水処理のシミュレーション方法、
〔７〕 被処理水が、窒素化合物を含有した排水である、前記〔１〕〜〔６〕いずれか１項に記載の生物学的水処理のシミュレーション方法、
〔８〕 活性汚泥と被処理水とを含有した被処理水相を有する生物反応槽中で、該活性汚泥により該被処理水を処理する工程を含む生物学的水処理をシミュレーションするシミュレーション装置であって、
活性汚泥に含まれ、かつ該被処理水中の処理対象物質の分解に関与する細菌の種類毎の細菌数を遺伝子解析法により決定する遺伝子解析手段と、
該遺伝子解析手段により決定された細菌の種類毎の細菌数から、遺伝子解析に基づく細菌濃度を算出する遺伝子解析ベース細菌濃度算出手段と、
該活性汚泥における処理対象物質の分解速度から活性を測定する活性測定手段と、
該細菌濃度と細菌の活性とから活性パラメータを算出する活性パラメータ算出手段と、
活性パラメータのデータが格納された活性パラメータデータベースと、
活性汚泥モデルを有し、活性パラメータデータベースに格納された活性パラメータのデータを参照し、入力された水処理プロセスの条件成分値と、生物反応槽の仕様と、生物反応槽の運転条件と、活性パラメータ算出手段により得られた下記式（４）で示される活性パラメータと、該遺伝子解析手段により決定された細菌の種類毎の細菌数とに基づき、下記式（５）又は式（６）で示される活性汚泥モデルにより、処理水質を求める処理水質演算手段と
を備えたことを特徴とする、生物学的水処理のシミュレーション装置、

（式中、ηは活性パラメータ、μmaxは最大比増殖速度［ｈｒ-1］であり、Ｃは基質濃度、Ｋは飽和定数であり、ｎは反応に関与する基質の数であり、Ｘ（Ｃｅｌｌ）は細菌数から求められた細菌の濃度［ｍｇ−ＣＯＤ／ｌ］を示す。）

（式中、ηは活性パラメータ、μmaxは最大比増殖速度［ｈｒ-1］であり、Ｃは基質濃度であり、Ｋは飽和定数であり、ｎは反応に関与する基質の数であり、Ｘ（Ｃｅｌｌ）は細菌数から求められた細菌の濃度［ｍｇ−ＣＯＤ／ｌ］であり、Ｐは反応阻害物質の濃度であり、ｍは、反応阻害物質の数を示す。）
〔９〕 該活性汚泥モデルが、ＡＳＭ３に基づいて改良されたものである、前記〔８〕記載の生物学的水処理のシミュレーション装置、
〔１０〕 該遺伝子解析手段が、リアルタイムＰＣＲにより、該細菌の種類毎の細菌数を決定する手段である、前記〔８〕または〔９〕記載の生物学的水処理のシミュレーション装置、
〔１１〕 該活性測定手段が、該処理対象物質の分解に関与する活性として、該処理対象物質の分解に関与する酸化活性および／または該処理対象物質の分解に関与する還元活性を測定する手段である、前記〔８〕〜〔１０〕いずれか１項に記載の生物学的水処理のシミュレーション装置、
〔１２〕 該処理対象物質の分解に関与する酸化活性が、アンモニア酸化活性と亜硝酸酸化活性とを含む硝化活性であり、該処理対象物質の分解に関与する還元活性が、硝酸還元活性と亜硝酸還元活性とを含む脱窒活性である、前記〔１１〕記載の生物学的水処理のシミュレーション装置、ならびに
〔１３〕 被処理水として、窒素化合物を含有した排水を処理する生物学的水処理をシミュレーションするためのものである、前記〔８〕〜〔１２〕いずれか１項に記載の生物学的水処理のシミュレーション装置、
に関する。 That is, the gist of the present invention is as follows.
[1] A simulation method for simulating biological water treatment including a step of treating the treated water with the activated sludge in a biological reaction tank having a treated water phase containing activated sludge and treated water. Yes,
(1) The following (1a) and (1b):
(1a) The number of bacteria included in the activated sludge and related to the decomposition of the substance to be treated in the treated water is determined by genetic analysis, and is calculated from the number of bacteria for each type of bacteria. (1b) the activity determined from the decomposition rate of the substance to be treated in the activated sludge,
An activity parameter represented by the following formula (4) calculated from:
(2) Condition component values of the water treatment process;
(3) The specifications of the target biological reaction tank,
(4) operating conditions of the biological reaction tank;
(5) the number of bacteria for each type of bacteria;
A biological water treatment simulation method, characterized by simulating treated water quality using an activated sludge model represented by the following formula (5) or formula (6) :

(Where η is the activity parameter, μmax is the maximum specific growth rate [hr-1], C is the substrate concentration, K is the saturation constant, n is the number of substrates involved in the reaction, and X (Cell ) Indicates the bacterial concentration [mg-COD / l] determined from the number of bacteria.)

(Where η is the activity parameter, μmax is the maximum specific growth rate [hr-1], C is the substrate concentration, K is the saturation constant, n is the number of substrates involved in the reaction, X (Cell) is the bacterial concentration [mg-COD / l] determined from the number of bacteria, P is the concentration of reaction inhibitory substance, and m is the number of reaction inhibitory substance.)
[2] (A) a step of determining the number of bacteria for each type of bacteria contained in the activated sludge and involved in the decomposition of the treatment target substance in the treated water by a genetic analysis method;
(B) calculating the bacterial concentration based on genetic analysis from the number of bacteria for each type of bacteria determined in the step (1),
(C) measuring the activity from the decomposition rate of the substance to be treated in the activated sludge,
(D) calculating the activity parameter from the bacterial concentration calculated in the step (B) and the activity calculated in the step (C); and (E) the activity parameter calculated in the step (D). Based on the condition component value of the water treatment process, the specifications of the target biological reaction tank, the operating conditions of the biological reaction tank, and the number of bacteria for each type of bacteria determined in the step (A). The process of simulating treated water quality using a sludge model,
The biological water treatment simulation method according to claim 1, comprising:
[3] The activated sludge model is an IWA activated sludge model NO. 3 (ASM3), the biological water treatment simulation method according to the above [1] or [2],
[4] The biological water treatment simulation method according to any one of [1] to [3], wherein the gene analysis method is real-time PCR,
[5] Bacteria that are involved in the degradation of the target substance to be treated and that exhibit the oxidizing ability and / or the bacteria that are involved in the degradation of the target substance and that exhibit the reducing ability And corresponding to the bacteria, the activity involved in the degradation of the substance to be treated is the oxidation activity involved in the degradation of the substance to be treated and / or the reducing activity involved in the degradation of the substance to be treated, [1] to [4] The biological water treatment simulation method according to any one of the above,
[6] The nitrification activity including ammonia oxidation activity and nitrite oxidation activity is measured as the oxidation activity, and the denitrification activity including nitrate reduction activity and nitrite reduction activity is measured as the reduction activity, [5] The biological water treatment simulation method according to [5],
[7] The biological water treatment simulation method according to any one of [1] to [6], wherein the water to be treated is waste water containing a nitrogen compound,
[8] A simulation apparatus for simulating biological water treatment including a step of treating the treated water with the activated sludge in a biological reaction tank having a treated water phase containing activated sludge and treated water. There,
Genetic analysis means for determining the number of bacteria for each type of bacteria contained in the activated sludge and involved in the decomposition of the substance to be treated in the treated water by a genetic analysis method;
From the number of bacteria for each type of bacteria determined by the genetic analysis means, a genetic analysis based bacterial concentration calculation means for calculating a bacterial concentration based on genetic analysis;
Activity measuring means for measuring activity from the decomposition rate of the substance to be treated in the activated sludge;
An activity parameter calculating means for calculating an activity parameter from the bacterial concentration and the activity of the bacteria;
An activity parameter database storing activity parameter data;
Have an activated sludge model, refer to the data of the activated parameters stored in the activated parameter database, input the condition component values of the water treatment process, the specifications of the biological reaction tank, the operating conditions of the biological reaction tank, and the activity Based on the activity parameter shown by the following formula (4) obtained by the parameter calculation means and the number of bacteria for each type of bacteria determined by the genetic analysis means, the following formula (5) or formula (6) is shown. A biological water treatment simulation device comprising: a treated water quality calculating means for obtaining treated water quality by an activated sludge model,

(Where η is the activity parameter, μmax is the maximum specific growth rate [hr-1], C is the substrate concentration, K is the saturation constant, n is the number of substrates involved in the reaction, and X (Cell ) Indicates the bacterial concentration [mg-COD / l] determined from the number of bacteria.)

(Where η is the activity parameter, μmax is the maximum specific growth rate [hr-1], C is the substrate concentration, K is the saturation constant, n is the number of substrates involved in the reaction, X (Cell) is the bacterial concentration [mg-COD / l] determined from the number of bacteria, P is the concentration of reaction inhibitory substance, and m is the number of reaction inhibitory substance.)
[9] The biological water treatment simulation apparatus according to [8], wherein the activated sludge model is improved based on ASM3.
[10] The biological water treatment simulation apparatus according to [8] or [9], wherein the gene analysis means is means for determining the number of bacteria for each type of bacteria by real-time PCR,
[11] Means in which the activity measuring means measures, as the activity involved in the decomposition of the substance to be treated, the oxidation activity involved in the decomposition of the substance to be treated and / or the reducing activity involved in the decomposition of the substance to be treated. The biological water treatment simulation device according to any one of [8] to [10],
[12] The oxidation activity involved in the decomposition of the treatment target substance is a nitrification activity including an ammonia oxidation activity and a nitrite oxidation activity, and the reduction activity involved in the decomposition of the treatment target substance is a nitrate reduction activity and a sublimation activity. The biological water treatment simulation apparatus according to the above [11], which has a denitrification activity including a nitrate reduction activity, and [13] a biological water treatment for treating wastewater containing a nitrogen compound as water to be treated The biological water treatment simulation apparatus according to any one of the above [8] to [12],
About.

  The biological water treatment simulation method of the present invention reflects the fluctuations in the number of bacteria of various microorganisms contained in activated sludge, the series of resolutions caused by the microorganisms, etc. There is an excellent effect that simulation can be performed with higher accuracy. In addition, the biological water treatment simulation apparatus of the present invention reflects the fluctuation of the number of bacteria of various microorganisms contained in the activated sludge, a series of resolution changes caused by the microorganisms, etc., and the behavior and treatment of the water treatment process. It has an excellent effect that the water quality can be simulated with higher accuracy.

The biological water treatment simulation method of the present invention includes a biological treatment tank including a step of treating the treated water with the activated sludge in a biological reaction tank having a treated water phase containing activated sludge and treated water. Simulation method for simulating water treatment
(1) The following (1a) and (1b):
(1a) The number of bacteria included in the activated sludge and related to the decomposition of the substance to be treated in the treated water is determined by genetic analysis, and is calculated from the number of bacteria for each type of bacteria. (1b) the activity determined from the decomposition rate of the substance to be treated in the activated sludge,
An activity parameter calculated from
(2) Condition component values of the water treatment process;
(3) The specifications of the target biological reaction tank,
(4) operating conditions of the biological reaction tank;
(5) the number of bacteria for each type of bacteria;
Based on the above, it is characterized by simulating treated water quality by an activated sludge model.

  In the present specification, the “activity determined from the decomposition rate of the target substance” has the same meaning as the activity involved in the decomposition of the target substance.

  In the simulation method of the present invention, the state of activated sludge is represented by a parameter representing a series of resolution of bacteria and the number of bacteria for each type of bacteria determined by the genetic analysis method, and the state of the activated sludge is: Incorporated into the activated sludge model, the treated water quality is predicted according to the model formula. Therefore, according to the simulation method of the present invention, it becomes possible to more accurately simulate the water treatment process and predict the treated water quality with higher accuracy.

  The simulation method of the present invention can satisfactorily reflect in the simulation a series of resolutions of bacteria that can change depending on factors such as salts and metals contained in wastewater, water temperature, extraction of activated sludge, and added chemicals. Therefore, according to the simulation method of the present invention, it becomes possible to more accurately simulate the water treatment process and predict the treated water quality with higher accuracy.

  In addition, according to the simulation method of the present invention, the activated sludge is represented by the number of bacteria and a series of bacteria decomposing ability. It is easy to predict whether the water is in the water, and it is effective for water quality improvement measures.

  Further, according to the simulation method of the present invention, since the state of activated sludge is represented by the parameter representing a series of resolution of bacteria and the number of bacteria for each type of bacteria determined by the gene analysis method, the series of bacteria is represented. It is possible to verify the factors that cause deterioration in the quality of treated water from the resolution of the number of bacteria and the time fluctuation history of the number of bacteria for each type of bacteria. For example, even if the number of bacteria is small, if the activity of bacteria is high and a treated water quality that achieves the standard is obtained, the conventional method can only see the treated water quality after the water treatment, It is determined that the process is proceeding smoothly. However, since the simulation method of the present invention can grasp the situation in which the number of bacteria is decreasing, it is possible to select an operation method that increases the number of bacteria in preparation for a case where the activity decreases. In addition, when the simulator is expanded to enable real-time water quality prediction, the conventional method can only see the treated water quality that is the result after water treatment. After being released, there is a drawback that it is difficult to respond adequately and it is impossible to judge whether the quality of treated water is temporary or continuous. However, according to the simulation method of the present invention, since the state of the bacterial group can be grasped, the deterioration of water quality can be dealt with accurately and quickly from the time fluctuation history of the state of the bacterial group.

  Furthermore, in the simulation method of the present invention, since the number of bacteria for each type of bacteria in the activated sludge is determined by the gene analysis method, the activated sludge is compared with, for example, that determined based on COD as in the prior art. The number of bacteria in it is expressed more quantitatively. Therefore, according to the simulation method of the present invention, biological water treatment can be simulated with high accuracy. In addition, according to the simulation method of the present invention, since the gene analysis method is used, for example, the state of activated sludge based on the type of bacteria is more improved than that determined based on COD as in the past. It can be reflected.

  The treated water is not particularly limited as long as it can be treated by biological water treatment. Examples thereof include domestic wastewater, basin end sewage, urban sewage, thermal power plant effluent, and factory effluent.

The condition component value of the water treatment process is not particularly limited. For example, dissolved oxygen [mg-O ₂ / l], soluble inert organic substance [mg-COD / l], easily decomposable water to be treated Organic substance [mg-COD / l], ammoniacal nitrogen [mg-N / l], nitrogen gas [mg-N / l], nitrate nitrogen [mg-N / l], nitrite nitrogen [mg-N] / L], alkalinity [moleHCO ₃ ⁻ / l], floating inert organic substance [mg-COD / l], slow-degrading organic substance [mg-COD / l], heterotrophic bacteria [mg-COD / l] And intracellular storage organic substances [mg-COD / l] of heterotrophic bacteria, nitrifying bacteria [mg-COD / l], suspended substances [mg-SS / l] and the like.

  Although it does not specifically limit as a specification of the said target biological reaction tank, For example, reaction tank capacity | capacitance, reaction tank fraction ratio, etc. are mentioned.

  Although it does not specifically limit as an operating condition of the said biological reaction tank, For example, blast volume, inflow water amount, return sludge amount, etc. are mentioned.

Specifically, as illustrated in the flowchart of FIG. 1, the simulation method of the present invention includes (A) a kind of bacteria that is contained in activated sludge and that is involved in the decomposition of the substance to be treated in the treated water. Determining the number of bacteria for each gene analysis method [gene analysis step S1],
(B) a step of calculating a bacterial concentration based on genetic analysis from the number of bacteria for each type of bacteria determined in the step (1) [gene analysis based bacterial concentration calculating step S2],
(C) a step of measuring the activity involved in the decomposition of the substance to be treated in the activated sludge [activity measurement step S3],
(D) a step of calculating an activity parameter from the bacterial concentration calculated in the step (B) and the bacterial activity calculated in the step (C) [activity parameter calculation step S4], and (E) the step The activity parameter calculated in (D), the condition component value of the water treatment process, the specifications of the target biological reaction tank, the operating conditions of the biological reaction tank, and the type of bacteria determined in the step (A) Based on the number of bacteria for each, the process of simulating the treated water quality by the activated sludge model [treated water quality calculation step S5],
It is a method including.

  Examples of the bacteria involved in the decomposition of the treatment target substance include bacteria that participate in the decomposition of the treatment target substance and exhibit an oxidizing ability, bacteria that participate in the decomposition of the treatment target substance and exhibit a reducing ability, and the like. . Such bacteria may be used alone or in combination.

Bacteria that exhibit oxidation ability by participating in the decomposition of the substance to be treated are not particularly limited, and examples thereof include ammonia-oxidizing bacteria and nitrite-oxidizing bacteria that are bacteria involved in nitrification activity. as is specifically Nitrosomonas (Nitrosomonas), nitroso Lactococcus (Nitrosococcus). Examples of the nitrite oxidizing bacteria, specifically, Nitrobacter (Nitrobacter), nitrous acid, such as Nitorosupira (Nitrospira) Examples include oxidizing bacteria.

Further, in the present invention, as a bacterium that exhibits the oxidation ability by participating in the decomposition of the treatment target substance, it is contained in the activated sludge and is involved in the decomposition of the organic substance that is the treatment target substance in the treated water. Bacteria that exhibit the above may be further used. Specific examples of bacteria that are included in the activated sludge and that exhibit oxidation ability by participating in the decomposition of organic substances that are treatment target substances in the treated water include, but are not limited to, for example, the genus Bacillus bacteria, Zooglea (Zoogloea) bacteria, such as Micrococcus (Micrococcus) bacteria and the like.

Bacteria that exhibit the reducing ability by participating in the decomposition of the treatment target substance are not particularly limited. For example, bacteria that are involved in denitrification activity, such as bacteria belonging to the genus Alcaligenes, bacteria belonging to the genus Azoarcus , Para' Lactococcus (Paracoccus) bacteria, such as Pseudomonas (Pseudomonas) bacteria and the like.

Further, in the present invention, the bacteria that are involved in the decomposition of the treatment target substance and exhibit the reduction ability are contained in the activated sludge, and are involved in the decomposition of the treatment target substance in the treated water and exhibit the reduction ability. Bacteria may also be used. The bacteria contained in the activated sludge and exhibiting the reducing ability by participating in the decomposition of the substance to be treated in the water to be treated are not particularly limited. For example, the substance to be treated is an organic halogen compound. if, bacteria with dehalogenation ability of such de Haro Cocco y des (Dehalococcoides) bacteria, if processed material is a sulfur compound such as sulfuric acid, sulfate-reducing bacteria, for example, Dess Le photo Makyu ram (Desulfotomaculum) genus Examples include bacteria, bacteria belonging to the genus Desulfobacter, bacteria belonging to the genus Desulfobacterium, and bacteria belonging to the genus Desulfovicrio .

  The gene analysis method is not particularly limited, and examples thereof include real-time PCR, competitive PCR, and MPN-PCR. Of these, real-time PCR is preferable from the viewpoint of rapidity. As the gene analysis method, when performing real-time PCR, the primer pairs are CTO 189fA / B [GGAGRAAAGCAGGGGATCG (SEQ ID NO: 1)] and CTO 189fC [GGAGGAAAGTAGGGGATCG (SEQ ID NO: 2)] for quantifying the number of ammonia oxidizing bacteria. Is a forward primer (for example, a mixture of CTO 189fA / B: CTO 189fC = 2: 1) and RT1r [CGTCCTCTCAGACCARCTACTG (SEQ ID NO: 3)] as a reverse primer, and a kind of nitrite-oxidizing bacteria A primer pair of NSR1113f [CCTGCTTTCAGTTGCTACCG (SEQ ID NO: 5)] and NSR1264r [GTTTGCAGCGCTTTGTACCG (SEQ ID NO: 6)] and the like can be mentioned as a nitrospira number quantifier, and narG1960f [TAYGTSGGSCARGARAA (sequence) No .: 8)] and narG2650r [TTYTCRTACCABGTBGC (SEQ ID NO: 9)] and the like, and for quantification of nitrite-reducing bacteria, irK876 [ATYGGCGGVAYGGCGA (SEQ ID NO: 10)] and irK1040 [GCCTCGATCAGRTTRTGGTT (SEQ ID NO: 9) : 11)], a primer pair of cd3aF [GTSAACGTSAAGGARACSGG (SEQ ID NO: 12)] and R3cd [GASTTCGGRTGSGTCTTGA (SEQ ID NO: 13)], and the like. Examples of the probe include TMP1 [CAACTAGCTAATCAGRCATCRGCCGCTC (SEQ ID NO: 4)] for quantification of ammonia-oxidizing bacteria, and NSR1143Taq [AGCACTCTGAAAGGACTGCCCAGG (SEQ ID NO: 7) for quantification of the number of nitrospira which is a kind of nitrite oxidizing bacteria. )] And the like.

For example, when the gene analysis method is real-time PCR, the number of bacteria is determined using, as an index, fluorescence signal intensity that increases in proportion to the amount of nucleic acid amplified based on the primer pair.
In addition, the number of bacteria for each type of bacteria is expressed by the formula (1):

Derived from.

  The calculation of the bacterial concentration based on the gene analysis from the number of bacteria is not particularly limited. For example, the formula (2):

It can be done by. The conversion factor can be calculated from the amount of oxygen consumed when bacteria are oxidatively decomposed.

  Examples of the activity involved in the decomposition of the treatment target substance include an oxidation activity involved in the decomposition of the treatment target substance, a reduction activity involved in the decomposition of the treatment target substance, and the like. Such activities may be alone or in combination.

  The oxidative activity involved in the decomposition of the substance to be treated is not particularly limited as long as it is based on the oxidative ability exhibited by the bacteria. For example, nitrification activity including ammonia oxidative activity and nitrite oxidative activity Etc.

  The reduction activity involved in the decomposition of the substance to be treated is not particularly limited as long as it is based on the reduction ability exhibited by the bacterium. For example, denitrification including nitrate reduction activity and nitrite reduction activity Activity and the like.

  In the simulation method of the present invention, nitrification activity including ammonia oxidation activity and nitrite oxidation activity, which are oxidation activities, is measured as the activity involved in the decomposition of the substance to be treated, and nitrate reduction activity and sublimation, which are reduction activities, are measured. In the case of measuring denitrification activity including nitrate reduction activity, in biological water treatment including nitrification step and denitrification step, the nitrification step is evaluated in two stages, ammonia oxidation step and nitrite oxidation step. The nitrogen process is evaluated in two stages, a nitrate reduction process and a nitrite reduction process. Therefore, with this simulation method, it is possible to more accurately simulate the water treatment process and predict the treated water quality with higher accuracy.

  In the simulation method of the present invention, nitrification activity including ammonia oxidation activity and nitrite oxidation activity, which are oxidation activities, is measured as the activity involved in the decomposition of the substance to be treated, and nitrate reduction activity and sublimation, which are reduction activities, are measured. When measuring denitrification activity including nitrate reduction activity, biological water treatment simulation of wastewater containing nitrogen compounds (for example, ammonia, organic nitrogen compounds, NOx compounds, etc.) can be performed with higher accuracy. .

  Examples of the activated sludge model used in the simulation method of the present invention include those obtained by improving ASM1, ASM2, ASM2d, ASM3, etc., which are IWA active models. Especially, it is preferable to improve based on ASM3 from the viewpoint of easy expansion of the model.

Specifically, as schematically illustrated in FIG. 2, the simulation apparatus of the present invention is a bioreactor having a treated water phase containing activated sludge and treated water. A simulation apparatus for simulating biological water treatment including a step of treating the treated water,
Genetic analysis means 11 for determining the number of bacteria for each type of bacteria contained in the activated sludge and decomposing the substance to be treated in the treated water by a genetic analysis method;
A genetic analysis-based bacterial concentration calculation means 12 for calculating a bacterial concentration based on genetic analysis from the number of bacteria for each type of bacteria determined by the genetic analysis means;
An activity measuring means 13 for measuring the activity involved in the decomposition of the substance to be treated in the activated sludge, an activity parameter calculating means 14 for calculating an activity parameter from the bacterial concentration and the bacterial activity,
An activity parameter database 15 in which activity parameter data is stored;
Having an activated sludge model, referring to the activated parameter data stored in the activated parameter database 15, the condition component value of the input water treatment process, the specification of the target treatment facility, the operating condition of the facility, Based on the activity parameter obtained by the activity parameter calculation means 14 and the number of bacteria for each type of bacteria determined by the gene analysis means 11, treated water quality calculation means 16 for obtaining treated water quality by the activated sludge model is provided. A simulation apparatus 10 is provided.

  The gene analyzing means 11 is not particularly limited, and examples thereof include means for determining the number of bacteria for each type of bacteria by real-time PCR, and examples of the real-time PCR apparatus include 7300 manufactured by Applied Biosystems. . The gene analysis means 11 determines the number of bacteria for each type of bacteria in the activated sludge by real-time PCR, and outputs the information to the gene analysis base bacteria concentration calculation means 12 and the like.

  In the genetic analysis-based bacterial concentration calculation means 12, information on the number of bacteria for each type of bacteria determined by the genetic analysis means 11 is input, and based on the input information, a bacterial concentration based on genetic analysis is calculated, The information is output to the activity parameter calculation means 14 and the like.

  Examples of the activity measuring means 13 include a means for measuring the activity involved in the decomposition of the substance to be treated in the activated sludge and outputting the result. In the activity measuring means, the activity is measured and output by an activity measuring method according to the type of degradation activity to be measured. The activity measuring means 13 is not particularly limited. For example, as the activity involved in the decomposition of the treatment target substance, the oxidation activity involved in the decomposition of the treatment target substance and / or the reduction involved in the decomposition of the treatment target substance. Means for measuring the activity and the like can be mentioned.

  For example, when simulating a biological water treatment including a nitrification step and a denitrification step as the biological water treatment, the activity measuring means 13 is used for ammonia oxidation activity and nitrite oxidation from the viewpoint of better simulation. A means for measuring nitrification activity including activity and denitrification activity including nitrate reduction activity and nitrite reduction activity is preferable. According to the activity measuring means of this aspect, biological water treatment for treating wastewater containing nitrogen compounds (for example, ammonia, organic nitrogen compounds, NOx compounds, etc.) as treated water can be simulated well. .

  The activity parameter calculation means 14 receives the information on the bacterial concentration calculated by the genetic analysis-based bacterial concentration calculation means 12 and the information on the bacterial activity calculated by the activity measurement means 13, and the bacterial concentration and Activity parameters are calculated from the activity of the bacteria, and the information is output to the activity parameter database 15, the treated water quality calculation means 16, and the like.

  In the activity parameter database 15, the activity parameter data calculated by the activity parameter calculation means 14 is accumulated, and the data stored in the activity parameter database 15 is referred to by the treated water quality calculation means 16 as appropriate. The

  In the treated water quality calculation means 16, the active parameters stored in the active parameter database 15 are based on parameters such as salts and metals contained in the water to be treated, water temperature of the biological treatment tank, extraction of activated sludge, and added chemicals. Based on the input condition component value of the water treatment process, the activity parameter obtained by the activity parameter calculation means 14, and the number of bacteria for each type of bacteria determined by the gene analysis method, The treated water quality is required by the activated sludge model.

  The activated sludge model is as described above, and ASM3 is preferable from the viewpoint of easy expansion of the model.

  Hereinafter, the present invention will be described in detail with reference to the drawings. However, the present invention is not limited to the drawings.

  FIG. 3 shows, as an example, an embodiment in which the biological water treatment simulation method of the present invention is applied to a wastewater treatment process of a thermal power plant that is an ammonia-containing wastewater treatment process.

  The wastewater treatment process of the thermal power plant shown in FIG. 3 includes a nitrification tank 1, a denitrification tank 2, an oxidation tank 3, and a solid-liquid separation tank 4, and the activated sludge of the nitrification tank 1 in the wastewater treatment process ( Nitrification sludge) and activated sludge (denitrification sludge) in denitrification tank 2 are collected and ammonia oxidation rate and nitrite oxidation in nitrification tank 1 are conducted by nitrification activity tests (ammonia oxidation rate test and nitrite oxidation rate test). And the nitrate reduction rate and the nitrite reduction rate in the denitrification tank 2 are measured by a denitrification activity test (nitrate reduction rate test and nitrite reduction rate test).

  The measurement of ammonia oxidation rate by bacteria contained in nitrified sludge (ammonia oxidation rate test) is performed as follows.

  In a 500 ml Erlenmeyer flask, 1 ml of dilution water [composition per liter: sodium bicarbonate 240 mg, BOD-A solution [according to paragraph 21 of JIS K 0102, pH 7.2]], BOD-B solution (JIS K 1 ml, BOD-C solution (calcium chloride solution according to item 21 of JIS K 0102) 1 ml, BOD-D solution [iron chloride (according to item 21 of JIS K 0102) III) Solution] 1 ml, balance water] 390 ml is added, and 10 ml of 1000 mg-N / l aqueous ammonium chloride solution is added to prepare mixture A. Next, the mixture A in the 500 ml Erlenmeyer flask is maintained at 30 ° C. in a thermostatic bath and aerated for 10 minutes or more with stirring to obtain a solution A. Here, the pH of the solution A is measured.

  500 ml of nitrified sludge is collected and solid-liquid separated by a centrifuge. The supernatant is removed from the obtained product, and the mixture is stirred and dispersed in 50 ml of the dilution water. The total volume of the obtained product is adjusted to 100 ml using the dilution water to obtain a nitrified sludge sample.

  Thereafter, 100 ml of the obtained nitrified sludge sample is put into the 500 ml flask and mixed with the solution A. Simultaneously with the mixing, 5 ml of the sample obtained by the mixing is sampled with a 5 ml syringe and filtered through a filter (manufactured by Advantech, trade name: glass fiber filter paper GF-75, pore size: 0.3 μm). Sampling is performed at regular intervals until ammoniacal nitrogen derived from ammonium chloride is consumed (about 2 hours).

  Further, immediately after mixing the nitrified sludge sample and the solution A, a 30 ml sample is taken separately from the sampling, and the sludge concentration is measured according to the item 14 of JIS K 0102.

  After ammoniacal nitrogen derived from ammonium chloride is consumed, the pH of the remaining mixture is measured and the sludge concentration is measured.

  The sample at each sampling time point is subjected to an ion chromatographic analysis method (according to the section 42.5 of JIS K 0102) to measure the amount of ammoniacal nitrogen. A change in the amount of ammoniacal nitrogen per unit time is calculated from the analysis result, and this is used as a decomposition rate to determine the ammonia oxidation rate.

  On the other hand, the measurement of nitrite oxidation rate (nitrite oxidation rate test) by bacteria contained in nitrified sludge is performed as follows.

  Into a 500 ml Erlenmeyer flask, 390 ml of the dilution water is added, and 10 ml of 1000 mg-N / l aqueous sodium nitrite solution is added to prepare a mixture B. Next, the mixture B in the 500 ml Erlenmeyer flask is maintained at 30 ° C. in a thermostatic bath and aerated for 10 minutes or more with stirring to obtain a solution B. Here, the pH of the solution B is measured.

  500 ml of nitrified sludge is collected and solid-liquid separated by a centrifuge. The supernatant is removed from the obtained product, and the mixture is stirred and dispersed in 50 ml of the dilution water. The total volume of the obtained product is adjusted to 100 ml using the dilution water to obtain a nitrified sludge sample.

  Thereafter, 100 ml of the obtained nitrified sludge sample is placed in the 500 ml flask and mixed with the solution B. Simultaneously with the mixing, 5 ml of the sample obtained by the mixing is sampled with a 5 ml syringe and filtered through a filter (manufactured by Advantech, trade name: glass fiber filter paper GF-75, pore size: 0.3 μm). Sampling is performed at regular intervals until nitrite nitrogen derived from sodium nitrite is consumed (about 2 hours).

  Further, immediately after mixing the nitrified sludge sample and the solution B, a 30 ml sample is taken separately from the sampling, and the sludge concentration is measured.

  After nitrite nitrogen derived from sodium nitrite is consumed, the pH of the remaining mixture is measured and the sludge concentration is measured.

  The amount of nitrite nitrogen is measured by performing an ion chromatographic analysis method (according to the section 43.1.2 of JIS K 0102) on the sample at each sampling time point. The change in the amount of nitrite nitrogen per unit time is calculated from the analysis result, and this is used as the decomposition rate to determine the nitrite oxidation rate.

  The measurement of nitrate reduction rate by bacteria contained in denitrified sludge (nitrate reduction rate test) is performed as follows.

  Into a 500 ml Erlenmeyer flask, 380 ml of the dilution water was added, and maintained at 30 ° C. in a thermostatic bath. While stirring, 10 ml of a 1000 mg-N / l aqueous sodium nitrate solution was added, and then an aqueous methanol solution [5000 mg methanol / l 10 ml is added to prepare mixture C. Thereafter, nitrogen gas is blown into the mixture C with an air balloon to deaerate for 10 minutes. Here, the pH of the mixture C is measured. A silicon stopper is put on the 500 ml Erlenmeyer flask, and nitrogen gas is blown into the 500 ml Erlenmeyer flask while stirring to remove air in the gas phase in the 500 ml Erlenmeyer flask. Thereafter, nitrogen gas is blown into a 1 liter Tedlar bag and placed in the silicon stopper of the 500 ml Erlenmeyer flask.

  500 ml of denitrified sludge is collected and solid-liquid separated by a centrifuge. The supernatant is removed from the obtained product, and the mixture is stirred and dispersed in 50 ml of the dilution water. The total volume of the obtained product is adjusted to 100 ml using the dilution water to obtain a denitrified sludge sample.

  Thereafter, 100 ml of the obtained denitrification sludge sample is put into the 500 ml flask and mixed with the mixture C. Simultaneously with the mixing, 5 ml of the sample obtained by the mixing is sampled with a 5 ml syringe and filtered through a filter (manufactured by Advantech, trade name: glass fiber filter paper GF-75, pore size: 0.3 μm). Sampling is performed at regular intervals until nitrate nitrogen derived from sodium nitrate is consumed (about 2 hours).

  Further, immediately after mixing the denitrified sludge sample and the mixture C, a 30 ml sample is taken separately from the sampling and the sludge concentration is measured.

  After the nitrate nitrogen derived from sodium nitrate is consumed, the pH of the remaining mixture is measured and the sludge concentration is measured.

  The amount of nitrate nitrogen is measured by performing an ion chromatographic analysis method (according to the section 43.2.5 of JIS K 0102) on the sample at each sampling time point. The change in the amount of nitrate nitrogen per unit time is calculated from the analysis result, and this is used as the decomposition rate to determine the nitrate reduction rate.

  On the other hand, the measurement of the nitrite reduction rate by bacteria contained in the denitrification sludge (nitrite reduction rate test) is measured as follows.

  In a 500 ml Erlenmeyer flask, 380 ml of the dilution water was added, maintained at 30 ° C. in a thermostatic bath, 10 ml of a 1000 mg-N / l sodium nitrite aqueous solution was added with stirring, and then an aqueous methanol solution [5000 mg methanol / l] Prepare mixture D by adding 10 ml. Thereafter, nitrogen gas is blown into the mixture D with a diffuser and deaerated for 10 minutes. Here, the pH of the mixture D is measured. A silicon stopper is put on the 500 ml Erlenmeyer flask, and nitrogen gas is blown into the 500 ml Erlenmeyer flask while stirring to remove air in the gas phase in the 500 ml Erlenmeyer flask. Thereafter, nitrogen gas is blown into a 1 liter Tedlar bag and placed in the silicon stopper of the 500 ml Erlenmeyer flask.

  500 ml of denitrified sludge is collected and solid-liquid separated by a centrifuge. The supernatant is removed from the obtained product, and the mixture is stirred and dispersed in 50 ml of the dilution water. The total volume of the obtained product is adjusted to 100 ml using the dilution water to obtain a denitrified sludge sample.

  Thereafter, 100 ml of the obtained denitrification sludge sample is put into the 500 ml flask and mixed with the mixture D. Simultaneously with the mixing, 5 ml of the sample obtained by the mixing is sampled with a 5 ml syringe and filtered through a filter (manufactured by Advantech, trade name: glass fiber filter paper GF-75, pore size: 0.3 μm). Sampling is performed at regular intervals until nitrite nitrogen derived from sodium nitrite is consumed (about 2 hours).

  Further, immediately after mixing the denitrified sludge sample and the mixture D, a 30 ml sample is taken separately from the sampling, and the sludge concentration is measured.

  After nitrite nitrogen derived from sodium nitrite is consumed, the pH of the remaining mixture is measured and the activated sludge concentration is measured.

  The amount of nitrite nitrogen is measured by performing an ion chromatographic analysis method (according to the section 43.1.2 of JIS K 0102) on the sample at each sampling time point. The change in the amount of nitrite nitrogen per unit time is calculated from the analysis result, and this is used as the decomposition rate to determine the nitrite reduction rate.

  In addition, the number of ammonia-oxidizing bacteria and nitrite-oxidizing bacteria in the nitrification tank are measured by real-time PCR, and the number of nitrate-reducing bacteria and nitrite-reducing bacteria in the denitrification tank are determined. taking measurement.

  Extraction of bacteria-derived DNA contained in activated sludge (nitrified sludge or denitrified sludge) is a technique used to extract DNA from soil, for example, crushing bacteria in activated sludge by physical means (beads, etc.) It can be performed by extracting DNA. The isolation of DNA is not particularly limited, and for example, trade name: FastDNA SPIN Kit for Soil (manufactured by Qbiogene), trade name: ISOIL for Beads Beating (manufactured by Nippon Gene Co., Ltd.) and the like are used. sell. Specifically, for example, when using trade name: ISOIL for Beads Beating (manufactured by Nippon Gene Co., Ltd.), DNA can be isolated from activated sludge as follows.

  Activated sludge (nitrified sludge or denitrified sludge) is collected from each reaction tank and placed in a 2 ml microcentrifuge tube. In addition, when the activated sludge solids concentration (MLSS concentration) is 1500 to 2000 mg / l, 2 ml of activated sludge, 2000 to 3000 mg / l, 1.5 ml of activated sludge, 3000 to 5000 mg / l In some cases, 1 ml of activated sludge, 5,000 to 7000 mg / l, 0.7 ml of activated sludge, 7000 to 10,000 mg / l, 0.5 ml of activated sludge is collected. Thereafter, the activated sludge placed in the microcentrifuge tube is subjected to 20630 × g (1500 rpm) for 2 minutes at 4 ° C. and 20630 × g (15000 rpm) for 30 seconds at 4 ° C. Next, the obtained activated sludge is suspended in 450 μl of Lysis Solution BB (trade name: attached to ISOIL for Beads Beating (manufactured by Nippon Gene Co., Ltd.)) preheated to 65 ° C. Thereafter, the obtained suspension is transferred to Beads Tube (trade name: attached to ISOIL for Beads Beating (manufactured by Nippon Gene Co., Ltd.)). In addition, the original tube is washed with 450 μl of Lysis Solution BB preheated to 65 ° C., and the suspension obtained after the washing is transferred to the Beads Tube. 50 μl of Lysis Solution 20S (trade name: attached to ISOIL for Beads Beating (manufactured by Nippon Gene Co., Ltd.)) is added to the suspension in the Beads Tube and mixed. Then, the obtained mixture is maintained at 65 ° C. for 15 minutes, and then subjected to beads beating at 3000 rpm for 90 seconds using a bead crusher [trade name: Beads Beater (manufactured by Nippon Gene)]. The resulting product is then maintained at 65 ° C. for 40 minutes with gentle mixing, then centrifuged at 12000 × g for 1 minute at 20 ° C. and about 660 μl of supernatant is collected in a 2 ml tube. 440 μl of Purification Solution (trade name: attached to ISOIL for Beads Beating (manufactured by Nippon Gene Co., Ltd.)) is added to the supernatant and mixed. Thereafter, 600 μl of chloroform is added and gently stirred, and then 900 μl of the aqueous layer is collected in a 2 ml tube by centrifugation at 12000 × g for 15 minutes at 20 ° C. An equal amount (900 μl) of Precipitation Solution (trade name: attached to ISOIL for Beads Beating (manufactured by Nippon Gene Co., Ltd.)) is added to the obtained product and mixed. The resulting product is centrifuged and the resulting precipitate is washed with Wash Solution. Thereafter, 1 ml of 70% by volume ethanol and 2 μl of trade name: Ethachinate (manufactured by Nippon Gene Co., Ltd.) are added to the resulting precipitate, and ethanol precipitation is performed to obtain a DNA precipitate. To the resulting DNA precipitate, 200 μl of TE buffer (composition: 10 mM Tris-HCl (pH 8.0), 0.1 mM EDTA) is added to dissolve the DNA to obtain a DNA sample for PCR. Such DNA samples are quantified.

  The number of bacteria of various bacteria contained in the activated sludge (nitrified sludge or denitrified sludge) can be quantified by, for example, various nucleic acid detection methods represented by real-time PCR. When quantifying the number of bacteria of various bacteria contained in activated sludge by the real-time PCR, quantification is performed using a nucleic acid sample extracted from the activated sludge and a primer pair and a probe suitable for the bacteria contained in the activated sludge. By performing the reaction under PCR conditions (temperature, time, cycle) suitable for amplification of the nucleic acid of the target bacteria, various bacteria and the number of bacteria contained in the activated sludge are quantified. Examples of the primer pair include CTO 189fA / B, CTO 189fC, and RT1r for quantifying ammonia oxidizing bacteria, and NSR1113f and NSR1264r for quantifying Nitrospira, which is a kind of nitrite-reducing bacteria. Examples of the probe include NMP1143Taq and the like for quantification of TMP1 and Nitrospira number which is a kind of nitrite-oxidizing bacteria for quantification of ammonia-oxidizing bacteria. Specifically, for example, the numbers of ammonia-oxidizing bacteria, nitrite-oxidizing bacteria, and eubacteria are as follows: CMO 189fA / B [GGAGRAAAGCAGGGGATCG (SEQ ID NO: 1)] and CTO 189fC [GGAGGAAAGTAGGGGATCG (SEQ ID NO: 1) : 2)] as a forward primer [for example, a mixture of CTO 189fA / B: CTO 189fC = 2: 1] and RT1r [CGTCCTCTCAGACCARCTACTG (SEQ ID NO: 3)] as a reverse primer, and TMP1 [CAACTAGCTAATCAGRCATCRGCCGCTC (sequence No .: 4)] Primer / probe set having a probe; for nitrite-oxidizing bacteria, a primer pair of NSR1113f [CCTGCTTTCAGTTGCTACCG (SEQ ID NO: 5)] and NSR1264r [GTTTGCAGCGCTTTGTACCG (SEQ ID NO: 6)], and NSR1143Taq AGCACTCTGAAAGGACTGCCCAGG (SEQ ID NO: 7) can be quantified by TaqMan method using a primer / probe set and a probe]. Examples of each probe include those in which the 5 'end is labeled with FAM (6-carbofluorescein) and the 3' end is labeled with TAMRA (6-carboxymethylrhodamine).

In the real-time PCR, a calibration curve prepared using a sample having a concentration of 10 ⁷ , 10 ⁶ , 10 ⁵ , 10 ⁴ , 10 ³ , or 10 ² copies / 5 μl / 1 reaction is used. Specifically, the calibration curve is prepared using a recombinant plasmid obtained by amplifying a nucleic acid corresponding to a gene to be subjected to real-time PCR by PCR and then cloning it into a plasmid vector. For example, in the case of a nitrite-oxidizing bacterium, a 16S rRNA gene specific to the nitrite-oxidizing bacterium is amplified using a primer pair of NSR1113f and NSR1264r, and the resulting product is cloned into a plasmid vector. The plasmid was used as a standard for preparing a calibration curve. The real-time PCR is performed using a standard sample with a known concentration (number of genes) and DNA purified from the sample (1 ng or 10 ng) as a template. Usually, the real-time PCR is carried out by using a 16S rRNA gene or a gene encoding an enzyme involved in water purification, such as the 16S rRNA gene of ammonia oxidizing bacteria [Appl. Environ. Microbiol. , 2001, Vol. 67, pp. 972-976], 16S rRNA gene of nitrospira which is a kind of nitrite oxidizing bacteria [Environ. Sci. Technol. , 2003, 37, 343-351], narG (nitrate reductase) gene of nitrate-reducing bacteria [Appl. Environ. Microbiol. , 2002, Vol. 68, pp. 6121 to 6128], nitrS (cytochrome cd1-type nitrite reductase) gene [FEMS Microbiology Ecology 2004, Vol. 49, p. 401] To 417], irK (copper-containing nitrite reductase) gene [J. Microbiol. Methods. , 2004, Vol. 59, pp. 327 to 335].

  The Ct value of each standard sample concentration (the point where the threshold and the PCR amplification curve intersect) is calculated, and a calibration curve is created from the relationship between the Ct value and the concentration. On the other hand, the Ct value of the sample DNA is also obtained and applied to a calibration curve prepared from the standard sample, thereby obtaining the copy number of the gene per 1 ng of the sample DNA used for real-time PCR or 10 ng. Finally, for example, the number of bacteria per 1 ml of activated sludge is expressed by the following formula (1):

Derived from.

  In addition, since the number of genes present in one bacterial cell differs depending on the type of bacteria, the target gene for real-time PCR is calculated by dividing the number of bacteria obtained from the above formula (1) by the number of genes. Can be calculated.

  From the number of bacteria obtained by the real-time PCR method, the formula (2):

Based on the above, the concentration [mg-COD / l] of bacteria (ammonia oxidizing bacteria, nitrite oxidizing bacteria, nitrate reducing bacteria or nitrite reducing bacteria) is determined. The dry weight per bacterium includes measured values or literature values [examples of literature values: 0.28 pg / cell, Appl. Environ. Values such as Microbiol (2002), 68, 245-253) are used. Further, the conversion factor is expressed by the formula (3):

From this, it can be calculated by dividing the oxygen consumption of bacteria (5 × 32) by the molecular weight (113). In this case, the conversion factor is 1.416.

  Thereafter, corresponding to each of ammonia oxidation, nitrite oxidation, nitrate reduction, and nitrite reduction, the activity parameter η is expressed by equation (4):

Ask for. Corresponding to each of ammonia oxidation, nitrite oxidation, nitrate reduction and nitrite reduction, activity parameters η evaluated over a certain period are accumulated, and a database is constructed.

  The activated parameter η and the number of bacteria obtained by the gene analysis method are introduced into the activated sludge model. Specifically, for example, the activity parameter and the number of bacteria obtained by gene analysis are introduced into the reaction rate equations for the growth of nitrifying bacteria (nitrification) and the growth (denitrification) of heterotrophic bacteria (denitrification bacteria). The reaction rate ρ of nitrification or denitrification in the activated sludge model is expressed by equation (5):

(Where η is the activity parameter, μmax is the maximum specific growth rate [hr-1], C is the substrate concentration, K is the saturation constant, n is the number of substrates involved in the reaction, and X (Cell ) Indicates the bacterial concentration [mg-COD / l] determined from the number of bacteria. Here, the saturation constant K is given to each substrate and has the same unit as each substrate. Experimental values, literature values, and theoretical values are used as the maximum specific growth rate [hr-1] μmax.

In addition, when there is a reaction inhibiting substance in activated sludge or waste water, the denitrification reaction rate ρ ′ is
Formula (6):

(Where η is the activity parameter, μmax is the maximum specific growth rate [hr-1], C is the substrate concentration, K is the saturation constant, n is the number of substrates involved in the reaction, X (Cell) is the bacterial concentration [mg-COD / l] determined from the number of bacteria, P is the concentration of reaction inhibitory substance, and m is the number of reaction inhibitory substance.)
Is required.

  Although it does not specifically limit as said reaction inhibitor, For example, chlorine etc. are mentioned.

  Next, reaction tank conditions (capacity, reaction tank temperature) and operation conditions (blowing volume, return activated sludge volume, and activated sludge extraction volume) are input to the water quality arithmetic unit input unit.

Next, the inflow amount and the inflow water quality are input to the water quality calculation device input unit. The influent water quality includes dissolved oxygen [mg-O ₂ / l], soluble inert organic substance [mg-COD / l], readily decomposable organic substance [mg-COD / l], ammoniacal nitrogen [mg-N / L], nitrogen gas [mg-N / l], nitrate nitrogen [mg-N / l], nitrite nitrogen [mg-N / l], alkalinity [moleHCO ₃ ⁻ / l], floating inertness Organic substance [mg-COD / l], slow-degrading organic substance [mg-COD / l], heterotrophic bacteria [mg-COD / l], intracellular storage organic substance of heterotrophic bacteria [mg-COD / l] , Nitrifying bacteria [mg-COD / l], suspended matter [mg-SS / l].

  Thereafter, the coal type is input to the water quality calculation device input unit. Since the type and concentration of the reaction inhibitor depend on the coal type, it is advantageous in that the activity parameter can be reflected more accurately by inputting the coal type.

  The bacterial weight is calculated from the number of bacteria obtained by the real-time PCR method, and is used as the initial value of the activated sludge in the reaction tank.

  From the operating conditions such as the coal type, the activity parameter is determined by referring to the activity parameter η database, and the reaction rate equation of the process involved in nitrification / denitrification of the activated sludge model deformed based on ASM3 or ASM3 The number of bacteria in the activated sludge and the quality of the treated water are determined by performing a simulation with an arithmetic unit using the activated sludge model incorporating the equation (6).

  FIG. 4 shows, as an example, an embodiment in which the biological water treatment simulation method of the present invention is applied to a water treatment process in a sewage treatment plant.

  The activated sludge in the reaction tank 5e in the water treatment process of the sewage treatment plant shown in FIG. 4 (reaction tanks 5a, 5b, 5c, 5d, 5e and the solid-liquid separation tank 6 adopting the standard activated sludge method) is collected, and Similarly, ammonia oxidation rate and nitrite oxidation rate were measured by nitrification activity test (ammonia oxidation rate test and nitrite oxidation rate test), and denitrification activity test (nitrate reduction rate test and nitrite reduction rate test). The nitrate reduction rate and the nitrite reduction rate are measured. Similarly to the above, the number of bacteria of each of ammonia-oxidizing bacteria, nitrite-oxidizing bacteria, nitrate-reducing bacteria, and nitrite-reducing bacteria is measured by a real-time PCR method as a gene analysis method.

  In the same manner as described above, the activation parameter η is obtained based on the equation (6). Also, the activity parameter η evaluated over a certain period is accumulated, and a database is constructed.

  Similarly to the above, the active parameter η and the number of bacteria obtained by the gene analysis method are introduced into the activated sludge model.

  Similarly to the above, initial values such as reaction tank conditions, operation conditions, inflow, inflow water quality, reaction tank activated sludge and the like are input to the water quality arithmetic unit input unit. Next, referring to the activity parameter η database from the operating conditions, the activity parameter is determined, and the reaction rate equation of the process involved in nitrification / denitrification of the activated sludge model deformed based on ASM3 or ASM3 is A simulation is performed by an arithmetic unit using an activated sludge model incorporating (6) to determine the number of bacteria in the activated sludge and the quality of treated water.

The target was a sewage treatment facility with a flow rate of 7500 m ³ / day, an effective capacity of all 5 reaction vessels: 2800 m ³ , and its fractional ratio (volume ratio) = 1: 1: 1: 1: 0.7. The standard activated sludge method is adopted, the aeration (aeration) of the first tank (reaction tank 5a) is stopped, and the second tank to the fifth tank (reaction tanks 5b, 5c, 5d, 5e) are aerated. ing. The sewage treatment facility is a facility schematically shown in FIG. The first sedimentation basin overflow water (inflow water) and the solid-liquid separation tank overflow water (treatment water) of the sewage treatment facility were sampled for 1 hour each, and the quality of the inflow water and the treated water was analyzed. The results are shown in Table 1.

  Further, activated sludge (nitrified sludge) in the fifth tank (reaction tank 5e) was collected once every two weeks.

  The ammonia oxidation rate and nitrite oxidation rate of the collected activated sludge (nitrified sludge) were measured according to the activity rate test method of the sewer test method as follows.

  In a 500 ml Erlenmeyer flask, dilute water [composition per liter: sodium hydrogen carbonate 240 mg, BOD-A solution [according to paragraph 21 of JIS K 0102, buffer solution (pH 7.2)] 1 ml, BOD-B solution (JIS 1 ml of magnesium sulfate solution according to item 21 of K 0102), 1 ml of BOD-C solution (calcium chloride solution according to item 21 of JIS K 0102), iron chloride according to item 21 of BOD-D solution (according to item 21 of JIS K 0102) (III) Solution) 1 ml, balance water] 390 ml was added, and 10 ml of 1000 mg-N / l aqueous ammonium chloride solution was added to prepare a mixture A. Next, the mixture A in the 500 ml Erlenmeyer flask was maintained at 20 ° C. in a thermostatic bath and aerated for 10 minutes or more with stirring to obtain a solution A. Here, the pH of the solution A was measured.

  500 ml of nitrified sludge was collected and subjected to solid-liquid separation of the nitrified sludge using a centrifuge. The supernatant was removed from the obtained product, and the mixture was stirred and dispersed in 50 ml of the diluted water. The total volume of the obtained product was adjusted to 100 ml using the dilution water, and a nitrified sludge sample was obtained. 100 ml of the obtained nitrified sludge sample was placed in the 500 ml flask and mixed with the solution A. Simultaneously with the mixing, 5 ml of the sample obtained by the mixing was sampled with a 5 ml syringe and filtered with a filter (manufactured by Advantech, trade name: glass fiber filter paper GF-75, pore size: 0.3 μm). Sampling was performed at regular intervals until ammoniacal nitrogen derived from ammonium chloride was consumed (about 2 hours).

  Further, immediately after mixing the nitrified sludge sample and the solution A, a 30 ml sample was taken separately from the sampling, and the sludge concentration was measured in accordance with item 14 of JIS K 0102.

  After ammoniacal nitrogen derived from ammonium chloride was consumed, the pH of the remaining mixture was measured and the sludge concentration was measured.

  The sample at each sampling time point is subjected to an ion chromatographic analysis method (according to the section 42.5 of JIS K 0102) to measure the amount of ammoniacal nitrogen. The change in the amount of ammoniacal nitrogen per unit time was calculated from the analysis results, and this was used as the decomposition rate to determine the ammonia oxidation rate.

  On the other hand, 390 ml of the diluted water was put into a 500 ml Erlenmeyer flask, and 10 ml of 1000 mg-N / l sodium nitrite aqueous solution was added to prepare a mixture B. Next, the mixture B in the 500 ml Erlenmeyer flask was maintained at 30 ° C. in a thermostatic bath and aerated for 10 minutes or more with stirring to obtain a solution B. Here, the pH of the solution B was measured.

  500 ml of nitrified sludge was collected and subjected to solid-liquid separation of the nitrified sludge using a centrifuge. The supernatant was removed from the obtained product, and the mixture was stirred and dispersed in 50 ml of the diluted water. The total volume of the obtained product was adjusted to 100 ml using the dilution water, and a nitrified sludge sample was obtained.

  Thereafter, 100 ml of the obtained nitrified sludge sample was placed in the 500 ml flask and mixed with the solution B. Simultaneously with the mixing, 5 ml of the sample obtained by the mixing was sampled with a 5 ml syringe and filtered with a filter (manufactured by Advantech, trade name: glass fiber filter paper GF-75, pore size: 0.3 μm). Sampling was performed at regular intervals until nitrite nitrogen derived from sodium nitrite was consumed (about 2 hours).

  Further, immediately after mixing the nitrified sludge sample and the solution B, a 30 ml sample was taken separately from the sampling, and the sludge concentration was measured.

  After nitrite nitrogen derived from sodium nitrite was consumed, the pH of the remaining mixture was measured and the sludge concentration was measured.

  The amount of nitrite nitrogen was measured by performing an ion chromatographic analysis method (according to section 43.1.2 of JIS K 0102) on the sample at each sampling time point. The change in the amount of ammoniacal nitrogen per unit time was calculated from the analysis results, and this was used as the decomposition rate to determine the nitrite oxidation rate.

  Moreover, about the bacteria contained in activated sludge, it analyzed by real-time PCR as follows. The purification of total DNA was performed using a trade name: ISOIL for Beads Beating (manufactured by Nippon Gene Co., Ltd.). The number of ammonia-oxidizing bacteria and nitrite-oxidizing bacteria was analyzed by real-time PCR. The number of ammonia-oxidizing bacteria was quantified by the TaqMan method using a primer / probe set consisting of CTO 189fA / B, CTO 189fC, RT1r, and TMP1. The number of nitrite-oxidizing bacteria was quantified by the TaqMan method using a primer / probe set consisting of NSR1113f, NSR1264r and NSR1143Taq.

  FIG. 5 shows the ammonia oxidation rate and nitrite oxidation rate on each measurement day in the water treatment process of the sewage treatment plant. In the figure, circles indicate the ammonia oxidation rate, and triangles indicate the nitrite oxidation rate. FIG. 6 shows the number of bacteria (based on the gene analysis method) and the activated sludge concentration involved in nitrification in the water treatment process of the sewage treatment plant. In the figure, circles indicate ammonia oxidizing bacteria, triangles indicate nitrite oxidizing bacteria, and squares indicate activated sludge concentration. Fig. 7 shows the concentration of ammonia-oxidizing bacteria, and Fig. 8 shows the concentration of nitrite-oxidizing bacteria. In the figure, circles indicate the bacterial concentration based on the activity test (mg-COD / l), and squares indicate the bacterial concentration based on the gene analysis method (mg-COD / l). In the literature [H. Furumai et al., Indian J. et al. Eng. Materials Sci. Vol. 5, pp. 173 to 181 (1998)], the maximum specific growth rate / growth yield for ammonia oxidation is 0.067 [mg-N / mg-COD / hr], nitrite oxidation The maximum specific growth rate / growth yield was 0.29 [mg-N / mg-COD / hr].

From FIG. 5, the difference between the maximum value and the minimum value of the ammonia oxidation rate is 2.1 mg-N / l / hr, and the nitrite oxidation rate is 1.6 mg-N / l / hr. .
On the other hand, when looking at the number of bacteria, ammonia oxidizing bacteria are on the order of 10 ⁸ . Nitrite-oxidizing bacteria have been on the order of 10 ⁸ from the latter half of 10 ⁷ . From the above, on each measurement day, each speed and the number of bacteria did not necessarily correspond. That is, it was found that the maximum oxidation rate did not depend only on the number of bacteria. Furthermore, as FIG. 6 shows, since the change of activated sludge density | concentration and the change of the number of bacteria do not respond | correspond, it turns out that the activated sludge density | concentration does not reflect the number of bacteria.

  Moreover, as shown in FIGS. 7 and 8, the magnitude of the bacterial concentration (mg-COD / l) based on the activity test does not correspond to the bacterial concentration (mg-COD / l) based on the gene analysis method. I understand that.

  Further, in accordance with each of ammonia oxidation and nitrite oxidation, the activity parameter η is expressed by the formula (4):

I asked for it. The result is shown in FIG.

  As a result, as shown in FIG. 9, it can be seen that the activity parameter reflects a change in activity and a change in the number of bacteria.

(Test Example 1)
In order to confirm only the effect of the activation parameter, the nitrite process is not added, and the denitrification process uses the conventional activated sludge model equation (specifically, the equation that does not introduce the activation parameter), and the nitrification process The calculation was carried out by introducing the activity parameter only into. The object was a sewage treatment plant, ASM3 was used as the base activated sludge model, and the recommended value of ASM3 at a water temperature of 20 ° C. was used as the reaction kinetic constant.

The target sewage treatment plant was the same as described in Example 1, the amount of influent water was 7500 m ³ / day, the effective capacity of all five reaction tanks was 2800 m ³ , and the fractionation ratio was 1: 1: 1. 1: 0.7. In the sewage treatment plant, the standard activated sludge method is adopted, but the aeration of the first tank (reaction tank 5a in FIG. 4) was stopped. The return sludge extraction amount was calculated as 3500 m ³ / day, and the excess sludge extraction amount was calculated as 120 m ³ / day. MLSS was about 1500 mg / l, and the dissolved oxygen amount was about 1.0 mg / l.

Assuming that the nitrification process is rate-limited to the nitrite oxidation process, the nitrite oxidation rate of 2.6 mg-N / l / hr obtained in the experiment on May 11 (first day) in Example 1 and nitrite Using the number of oxidized bacteria 2.6 × 10 ¹⁰ cells / l, the maximum specific growth rate 0.042 hr ^−1, and the growth yield 0.24 mg-COD / mg-N, the activity parameter η is expressed by the formula (7) :

Calculated with

The influent water quality is dissolved oxygen 0 mg-O ₂ / l, soluble inert organic material 15 mg-COD / l, readily decomposable organic material 30 mg-COD / l, ammoniacal nitrogen 8.3 mg-N / l, nitrogen gas 0 mg -N / l, nitrate nitrogen 0mg-N / l, alkalinity 30moleHCO ₃ ^- / l, suspended in an inert organic substances 12mg-COD / l, slow degradable organic substances 50mg-COD / l, heterotrophic bacteria 15 mg-COD / L, intracellular storage organic substance of heterotrophic bacteria 0 mg-COD / l, nitrifying bacteria 0 mg-COD / l, suspended substance 100 mg-SS / l. Table 2 shows the results when the activity parameters were introduced (Example 2), the results when the recommended values of ASM3 were used (Comparative Example 1), and the measurement results (May average) (Reference Example 1).

As a result, as shown in Table 2, in the case of Comparative Example 1 (using the recommended value of ASM3), since NH ₄ —N is lower than the measurement result, a result in which the nitrification reaction proceeds too much is obtained. It was. Thus, conventionally, the reaction kinetic constants such as the maximum specific growth rate are adjusted by trial and error so as to match the measurement result (Reference Example 1). When parameters are introduced, the prediction accuracy can be improved with a small number of trials. Furthermore, since the reaction kinetic constant can be determined with a small number of trials, there is an effect of increasing the working efficiency. In addition, in the past, experience was also required for calibration to adjust the kinetic constants, but by using genetic analysis, even engineers with little experience can perform highly accurate simulations. Can do.

  The present invention allows for more efficient and cost effective implementation of biological water treatment.

FIG. 1 is a flowchart showing one embodiment of the biological water treatment simulation method of the present invention. FIG. 2 is a flowchart showing an embodiment of the biological water treatment simulation apparatus of the present invention. FIG. 3 is a schematic diagram of a wastewater treatment process of a thermal power plant. FIG. 4 is a schematic diagram of a water treatment process in a sewage treatment plant. FIG. 5 is a diagram showing the nitrification rate on each measurement day in the water treatment process at the sewage treatment plant. In the figure, circles indicate the ammonia oxidation rate, and triangles indicate the nitrite oxidation rate. FIG. 6 is a diagram showing the number of bacteria involved in nitrification on each measurement day in the water treatment process at the sewage treatment plant. In the figure, circles indicate ammonia oxidizing bacteria, triangles indicate nitrite oxidizing bacteria, and squares indicate activated sludge concentration. FIG. 7 is a diagram showing the ammonia-oxidizing bacteria concentration on each measurement day. In the figure, circles indicate the bacterial concentration based on the activity test (mg-COD / l), and squares indicate the bacterial concentration based on the gene analysis method (mg-COD / l). FIG. 8 is a diagram showing the nitrification rate of nitrite-oxidizing bacteria on each measurement day. In the figure, circles indicate the bacterial concentration based on the activity test (mg-COD / l), and squares indicate the bacterial concentration based on the gene analysis method (mg-COD / l). FIG. 9 is a diagram showing activity parameters on each measurement date. In the figure, circles indicate ammonia oxidation activity, and squares indicate nitrite oxidation activity.

Explanation of symbols

1 Nitrification tank 2 Denitrification tank 3 Oxidation tank 4, 6 Solid-liquid separation tank 5 Reaction tank

Claims (13)

In a biological reaction tank having a treated water phase containing activated sludge and treated water, a simulation method for simulating biological water treatment including a step of treating the treated water with the activated sludge,
(1) The following (1a) and (1b):
(1a) The number of bacteria included in the activated sludge and related to the decomposition of the substance to be treated in the treated water is determined by genetic analysis, and is calculated from the number of bacteria for each type of bacteria. (1b) the activity determined from the decomposition rate of the substance to be treated in the activated sludge,
An activity parameter represented by the following formula (4) calculated from:
(2) Condition component values of the water treatment process;
(3) The specifications of the target biological reaction tank,
(4) operating conditions of the biological reaction tank;
(5) the number of bacteria for each type of bacteria;
The biological water treatment simulation method characterized by simulating treated water quality using an activated sludge model represented by the following formula (5) or formula (6) :

(Where η is the activity parameter, μmax is the maximum specific growth rate [hr-1], C is the substrate concentration, K is the saturation constant, n is the number of substrates involved in the reaction, and X (Cell ) Indicates the bacterial concentration [mg-COD / l] determined from the number of bacteria.)

(Where η is the activity parameter, μmax is the maximum specific growth rate [hr-1], C is the substrate concentration, K is the saturation constant, n is the number of substrates involved in the reaction, X (Cell) is the bacterial concentration [mg-COD / l] determined from the number of bacteria, P is the concentration of reaction inhibitory substance, and m is the number of reaction inhibitory substance.) (A) a step of determining the number of bacteria for each type of bacteria contained in the activated sludge and involved in the decomposition of the substance to be treated in the treated water by a genetic analysis method;
(B) calculating the bacterial concentration based on genetic analysis from the number of bacteria for each type of bacteria determined in the step (1),
(C) measuring the activity from the decomposition rate of the substance to be treated in the activated sludge,
(D) calculating the activity parameter from the bacterial concentration calculated in the step (B) and the activity calculated in the step (C); and (E) the activity parameter calculated in the step (D). Based on the condition component value of the water treatment process, the specifications of the target biological reaction tank, the operating conditions of the biological reaction tank, and the number of bacteria for each type of bacteria determined in the step (A). The process of simulating treated water quality using a sludge model,
The biological water treatment simulation method according to claim 1, comprising:   The activated sludge model is IWA activated sludge model NO. The biological water treatment simulation method according to claim 1, which is an improvement based on 3 (ASM3).   The biological water treatment simulation method according to claim 1, wherein the gene analysis method is real-time PCR.   Bacteria involved in the degradation of the treatment target substance are bacteria that participate in the degradation of the treatment target substance and exert oxidation ability and / or bacteria that participate in the degradation of the treatment target substance and exert reduction ability, Corresponding to the bacteria, the activity involved in the degradation of the substance to be treated is an oxidative activity involved in the degradation of the substance to be treated and / or a reducing activity involved in the degradation of the substance to be treated. 5. The biological water treatment simulation method according to any one of 4 above.   6. The nitrification activity including ammonia oxidation activity and nitrite oxidation activity is measured as the oxidation activity, and the denitrification activity including nitrate reduction activity and nitrite reduction activity is measured as the reduction activity. Method of biological water treatment for the plant.   The biological water treatment simulation method according to claim 1, wherein the water to be treated is wastewater containing a nitrogen compound. In a biological reaction tank having a treated water phase containing activated sludge and treated water, a simulation device for simulating biological water treatment including a step of treating the treated water with the activated sludge,
Genetic analysis means for determining the number of bacteria for each type of bacteria contained in the activated sludge and involved in the decomposition of the substance to be treated in the treated water by a genetic analysis method;
From the number of bacteria for each type of bacteria determined by the genetic analysis means, a genetic analysis based bacterial concentration calculation means for calculating a bacterial concentration based on genetic analysis;
Activity measuring means for measuring activity from the decomposition rate of the substance to be treated in the activated sludge;
An activity parameter calculating means for calculating an activity parameter from the bacterial concentration and the activity of the bacteria;
An activity parameter database storing activity parameter data;
Have an activated sludge model, refer to the data of the activated parameters stored in the activated parameter database, input the condition component values of the water treatment process, the specifications of the biological reaction tank, the operating conditions of the biological reaction tank, and the activity Based on the activity parameter shown by the following formula (4) obtained by the parameter calculation means and the number of bacteria for each type of bacteria determined by the genetic analysis means, the following formula (5) or formula (6) is shown. A biological water treatment simulation apparatus comprising: a treated water quality calculating means for obtaining treated water quality using an activated sludge model.

(Where η is the activity parameter, μmax is the maximum specific growth rate [hr-1], C is the substrate concentration, K is the saturation constant, n is the number of substrates involved in the reaction, and X (Cell ) Indicates the bacterial concentration [mg-COD / l] determined from the number of bacteria.)

(Where η is the activity parameter, μmax is the maximum specific growth rate [hr-1], C is the substrate concentration, K is the saturation constant, n is the number of substrates involved in the reaction, X (Cell) is the bacterial concentration [mg-COD / l] determined from the number of bacteria, P is the concentration of reaction inhibitory substance, and m is the number of reaction inhibitory substance.)   9. The biological water treatment simulation apparatus according to claim 8, wherein the activated sludge model is improved based on ASM3.   The biological water treatment simulation apparatus according to claim 8 or 9, wherein the gene analysis means is means for determining the number of bacteria for each kind of bacteria by real-time PCR.   The activity measuring means is a means for measuring, as an activity involved in the decomposition of the substance to be treated, an oxidative activity involved in the decomposition of the substance to be treated and / or a reducing activity involved in the decomposition of the substance to be treated. The biological water treatment simulation apparatus according to any one of claims 8 to 10.   The oxidation activity involved in the decomposition of the treatment target substance is a nitrification activity including ammonia oxidation activity and nitrite oxidation activity, and the reduction activity involved in the decomposition of the treatment target substance is nitrate reduction activity and nitrite reduction activity. The biological water treatment simulation apparatus according to claim 11, which has a denitrification activity comprising:   The biological water treatment simulation apparatus according to any one of claims 8 to 12, which is for simulating biological water treatment for treating wastewater containing nitrogen compounds as water to be treated.

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