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WO2005030654A1 - Procede et appareil pour la nitrification - Google Patents

Procede et appareil pour la nitrification Download PDF

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Publication number
WO2005030654A1
WO2005030654A1 PCT/JP2004/014411 JP2004014411W WO2005030654A1 WO 2005030654 A1 WO2005030654 A1 WO 2005030654A1 JP 2004014411 W JP2004014411 W JP 2004014411W WO 2005030654 A1 WO2005030654 A1 WO 2005030654A1
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WO
WIPO (PCT)
Prior art keywords
nitrogen
nitrification
tank
concentration
raw water
Prior art date
Legal status (The legal status is an assumption and is not a legal conclusion. Google has not performed a legal analysis and makes no representation as to the accuracy of the status listed.)
Ceased
Application number
PCT/JP2004/014411
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English (en)
Japanese (ja)
Inventor
Kiyomi Arakawa
Akira Yamaguchi
Toshihiro Tanaka
Current Assignee (The listed assignees may be inaccurate. Google has not performed a legal analysis and makes no representation or warranty as to the accuracy of the list.)
Ebara Corp
Original Assignee
Ebara Corp
Priority date (The priority date is an assumption and is not a legal conclusion. Google has not performed a legal analysis and makes no representation as to the accuracy of the date listed.)
Filing date
Publication date
Application filed by Ebara Corp filed Critical Ebara Corp
Publication of WO2005030654A1 publication Critical patent/WO2005030654A1/fr
Anticipated expiration legal-status Critical
Ceased legal-status Critical Current

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Classifications

    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F3/00—Biological treatment of water, waste water, or sewage
    • C02F3/006—Regulation methods for biological treatment
    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F2209/00—Controlling or monitoring parameters in water treatment
    • C02F2209/06—Controlling or monitoring parameters in water treatment pH
    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F2209/00—Controlling or monitoring parameters in water treatment
    • C02F2209/22—O2
    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F3/00—Biological treatment of water, waste water, or sewage
    • C02F3/02—Aerobic processes
    • C02F3/06—Aerobic processes using submerged filters
    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F3/00—Biological treatment of water, waste water, or sewage
    • C02F3/30—Aerobic and anaerobic processes
    • C02F3/302—Nitrification and denitrification treatment
    • Y—GENERAL TAGGING OF NEW TECHNOLOGICAL DEVELOPMENTS; GENERAL TAGGING OF CROSS-SECTIONAL TECHNOLOGIES SPANNING OVER SEVERAL SECTIONS OF THE IPC; TECHNICAL SUBJECTS COVERED BY FORMER USPC CROSS-REFERENCE ART COLLECTIONS [XRACs] AND DIGESTS
    • Y02—TECHNOLOGIES OR APPLICATIONS FOR MITIGATION OR ADAPTATION AGAINST CLIMATE CHANGE
    • Y02W—CLIMATE CHANGE MITIGATION TECHNOLOGIES RELATED TO WASTEWATER TREATMENT OR WASTE MANAGEMENT
    • Y02W10/00—Technologies for wastewater treatment
    • Y02W10/10—Biological treatment of water, waste water, or sewage

Definitions

  • the present invention relates to a method for aerating and nitrifying various kinds of water to be treated (hereinafter referred to as “raw water”) such as waste liquid containing ammoniacal nitrogen under conditions where ammonia-oxidizing bacteria are present.
  • raw water such as waste liquid containing ammoniacal nitrogen under conditions where ammonia-oxidizing bacteria are present.
  • the present invention relates to a method and an apparatus for effectively controlling nitrification concentration (nitrite nitrogen concentration) by adjusting the concentration.
  • Ammoniacal nitrogen contained in wastewater is one of the causes of eutrophication in rivers, lakes and seas, etc., and it is necessary to remove it effectively using wastewater treatment processes.
  • the ammoniacal nitrogen in the waste liquid is first oxidized to nitrite nitrogen by ammonia oxidizing bacteria, and further, this nitrite nitrogen is oxidized to nitrate nitrogen by nitrite oxidizing bacteria.
  • Non-Patent Document 1 The biological denitrification process using this autotrophic bacterium is reported in [Non-Patent Document 1], and denitrification is progressing by the following reaction.
  • the following method is used to stop the oxidation of ammonia nitrogen by nitrite nitrogen and to suppress the action of nitrite-oxidizing bacteria so as to prevent the production of nitrate nitrogen.
  • the present invention solves the above-mentioned conventional problems, and comprises a method of performing nitrification treatment by supplying raw water containing ammoniacal nitrogen in a state where ammonia-oxidizing bacteria are present and supplying the raw water to a nitrification tank for aeration using an oxygen-containing gas. It is intended to provide a means that can control the concentration of nitrogen and nitrogen nitrite to an appropriate molar ratio.
  • the present invention provides a method for performing a nitrification treatment by supplying raw water containing ammonia nitrogen to a nitrification tank that performs aeration in the presence of ammonia-oxidizing bacteria. Knowing that the concentration of ammonia nitrogen that is oxidized to nitrite nitrogen changes, we found that the nitric acid concentration was adjusted by adjusting the M-alkalinity of the raw water. It is.
  • M-alkalinity (bicarbonate alkalinity) as used herein refers to the alkalinity [ ⁇ ⁇ 4.8] (total alkalinity or sewage test method, 1997 edition, p. 121). 1
  • the present invention has solved the above problems by the following means.
  • Detector for measuring M-alli strength and ammonia nitrogen concentration of raw water chemical injection device for adjusting M-alli strength of raw water, M-alkaline adjustment tank, and oxygen-containing gas Wastewater containing ammoniacal nitrogen, characterized in that it consists of a partial nitrification tank for ammoniacal nitrogen with a supply facility for the acid, and is characterized in that the acid or alkali from the chemical injection device is injected into the M-Al power adjustment tank.
  • Nitrification equipment for measuring M-alli strength and ammonia nitrogen concentration of raw water
  • chemical injection device for adjusting M-alli strength of raw water M-alkaline adjustment tank
  • oxygen-containing gas Wastewater containing ammoniacal nitrogen characterized in that it consists of a partial nitrification tank for ammoniacal nitrogen with a supply facility for the acid, and is characterized in that the acid or alkali from the chemical injection device is injected into the M-Al power adjustment tank.
  • Ammoniacal nitrogen with a detection unit that measures the M-alli power and ammoniacal nitrogen concentration of raw water, a chemical injection device for adjusting the M-alkaliness of raw water, and an oxygen-containing gas supply facility A nitrification treatment apparatus for wastewater containing ammoniacal nitrogen, wherein an acid or alkali from a chemical injection device is injected into the partial nitrification tank.
  • the partial nitrification tank is an upflow type reaction tank filled with a carrier, and the acid or alkali from the chemical injection device is injected into the circulation path of the partial nitrification tank. Nitrification process for wastewater containing ammoniacal nitrogen
  • the nitrification treatment is performed in a nitrification tank in which the concentration of dissolved oxygen is controlled while controlling the degree of M-Al power of the raw water.
  • Nitrite nitrogen can be controlled to the target concentration, and the nitrite oxidation reaction can be performed stably for a long period of time.
  • the nitric nitrogen and the ammonia nitrogen are adjusted to a desired molar ratio. Can be.
  • the ammoniacal nitrogen in the wastewater is partially nitrified, and the ammoniacal nitrogen and the nitrite nitrogen are mixed at a predetermined molar ratio (ie, 60:40 to 40: 6). 0), the dissolved oxygen concentration in the nitrification tank is adjusted, and the M-alkalinity of the raw water is adjusted to be a set multiple of the target nitrite nitrogen concentration, and the pH in the tank is adjusted. It is performed as a nitrification treatment method for wastewater containing ammonia nitrogen, which is characterized by being within a predetermined range (ie, pH 7.5 or less).
  • predetermined molar ratio is a range of a molar ratio of nitrite nitrogen to ammonia nitrogen, and a range suitable for supply to the denitrification treatment using an autotrophic bacterium.
  • predetermined range refers to a range of pH at which the generation rate of nitrite nitrogen is increased, and most preferably a range of pH at which the nitrite nitrogen is maximized. It was found that when oxidizing to nitrite nitrogen, the amount of M-Al nitrate was consumed at the same time, and the consumption was about 6 to 8 times, that is, about 7 times the amount of nitrite nitrogen generated.
  • This consumption of M-alkalinity occurs during the oxidation of ammonia nitrogen to nitrite nitrogen and is not consumed when oxidizing nitrite nitrogen to nitrate nitrogen. Therefore, it is important to suppress the production of nitrate nitrogen, that is, to make nitrite predominant in the environment inside the nitrification tank.
  • the amount of nitrite nitrogen generated is determined by the amount of M-Al ferrite flowing into the nitrification tank.
  • the concentration of ammonia nitrogen in the tank should be 50 to 1000 mg / liter, preferably 300 to 100 mg / liter in order to utilize the toxicity of free ammonia. It is desirable to process to liters. If the ammonia nitrogen in the tank exceeds 100 OmgZ liter, the concentration of free ammonia in the tank will increase, and the nitrite nitrogen generation activity will decrease significantly. If the ammonia nitrogen in the tank is less than 5 OmgZ liter, the concentration of free ammonia in the tank decreases, the activity of nitrite-oxidizing bacteria increases, and nitrate becomes dominant.
  • the dissolved oxygen concentration in the nitrification tank is important in order to make nitrite dominant, and it may be 3 mg / liter or less, preferably OmgZ liter instantaneously, but on average It is important to keep between 1.5 and 2.5 mg l.
  • the generation rate of nitrite nitrogen is maximum at pH 8.0 to 8.5, but when the ammonia nitrogen of raw water is high, nitrite nitrogen at pH 6.5 to 7.5 It was experimentally determined that the generation rate of the was maximized.
  • the temperature in the nitrification tank is also related, and the temperature in the nitrification tank is 10 to 40 ° C, preferably 3 When the temperature is 0 to 35 ° C, the activity can be kept high.
  • the SRT sludge retention time
  • the SRT sludge retention time
  • nitrite becomes predominant, and the nitrite nitrogen concentration of the treated water can be determined only by adjusting the concentration of the raw water M-Al-Hydrogen.
  • FIG. 1 is a flow sheet of a transient method using a biological carrier, which is an example of the treatment method of the present invention.
  • FIG. 2 shows a flow sheet of a biofilm filtration system as an example according to the treatment system of the present invention.
  • FIG. 3 is a flow sheet of an upward flow fluidized bed system as an example according to the treatment system of the present invention.
  • FIG. 4 is a flowchart illustrating a transient method using a biological carrier, which is an example of the treatment method of the present invention, in which the M-alkalinity adjusting tank is omitted.
  • FIG. 5 is a graph showing changes in the quality of raw water and treated water in Example 1.
  • FIG. 6 is a graph showing the relationship between the ratio of raw water M-degree of ferrite and the ammonia water and nitrite nitrogen in treated water in Example 2.
  • FIG. 7 is a graph showing the relationship between raw water M-alkalinity, raw water M-alkalinity, and the ratio of treated water nitrite nitrogen in Example 2.
  • FIG. 1 shows a flow sheet of a transient system using a biological carrier, which is an example of the treatment system of the present invention.
  • FIG. 2 shows another example of a flow sheet using biofilm filtration.
  • Raw water 16 is first charged into the M-alkalinity adjusting tank 2.
  • M—Alkalinity adjusting tank (also called raw water adjusting tank) 2 is equipped with a stirrer 15 for stirring.
  • a part of the raw water 16 in the raw water tank 2 is introduced into the M-alkalinometer 5 to measure the M-alkalinity.
  • an ammonia concentration meter 6 is also installed in the M-alkalinity adjusting tank 2, and the ammonia concentration of the raw water 16 is measured.
  • M—Alkalinity meter 5 Based on the measurement results of the ammonia concentration meter 6 and the results calculated by the arithmetic and control unit 7, to obtain an M-force of 6 to 8 times the target nitrite nitrogen concentration.
  • the alkali supply pump 13 or the acid supply pump 14 operates to adjust the M-alkalinity so as to add water or acid.
  • the raw water 16 whose M-alkalinity was adjusted to the target value was converted into the nitrification tank 1 by the raw water supply pump 4 (Note that the nitrification tank here is not a nitrification tank that is completely nitrified. It is a tank that performs nitrification.)
  • a total of 8 dissolved oxygen (DO) is installed in the nitrification tank 1 so that the dissolved oxygen in the nitrification tank 1 is 3 mg / liter or less, preferably 1.5 to 2.5 mg / liter.
  • the oxygen supply amount is controlled by adjusting the air volume of the blower 10 or by intermittently operating the blower.
  • the dissolved oxygen in the nitrification tank 1 is less than 0.5 mgZ liter, the oxygen becomes insufficient and the nitrification reaction does not proceed sufficiently. If the dissolved oxygen is more than 4.Omg / liter, the oxygen supply will be excessive and the amount of nitrate nitrogen generated will increase.
  • the amount of raw water input is controlled so that the nitrogen load is 3 kgN / m 3 ⁇ d or less, and the nitrification tank HRT for raw water 16 is set for 0.3 to 3 days.
  • the toxicity of free ammonia is used, so the ammonia nitrogen concentration in the tank is 50 to 100 Omg / liter, preferably 300 to 1000 mgZ liter. It is desirable that the temperature in the nitrification tank 1 is also related. When the temperature in the nitrification tank 1 is set to 10 to 40 ° C, preferably 30 to 35 ° C, it is easy to perform control.
  • the concentration of nitrite nitrogen can be adjusted to any concentration.
  • the required amount of ammonia nitrogen in the raw water 16 becomes nitrite nitrogen and is discharged from the nitrification tank.
  • Nitrification tank 1 is a transient method (Fig. 1) in which only raw water is aerated, and a transient method using biological carriers.
  • Fig. 1 biofilm filtration system (floating media ⁇ immersion media)
  • Fig. 2 upward flow fluidized bed system using biocarriers
  • Fig. 3 solid-liquid Any type such as an activated sludge system equipped with a separation device or an activated sludge using a biological carrier and a microorganism carrier can be used. Since it is more advantageous to reduce the amount of suspended sludge in the nitrification tank 1 in order to control nitrite to predominate over nitrate, one of these methods is a temporary method in which only raw water is aerated.
  • the method (chemostat method), the transient method using a biological carrier, and the biofilm filtration method (floating filter material ⁇ immersion filter material).
  • the HRT is set to 0.3 to 3 days.
  • Fig. 3 shows a flow sheet for controlling the M-alkali level by adding a chemical for adjusting the M-alkali level to the nitrification tank.
  • the M-alkalinity and the ammonia nitrogen concentration of the raw water 16 are measured in the M-alkalinity measuring tank 3 by the M-allimeter 5 and the ammonia concentration meter 6. Based on the results calculated by the arithmetic and control unit 7, the alkaline aqueous solution or the acidic aqueous solution is subjected to an alkaline force so that the M-alkalinity is 6 to 8 times the target nitrite nitrogen concentration. It may be added to the nitrification tank 1 using a re-supply pump 13 or an acid supply pump 14. Examples>
  • Fig. 1 shows the case where the biological carrier is not charged into the nitrification tank 1.
  • the capacity of the nitrification tank 1 is 100 liters.
  • Table 1 shows the water quality of the anaerobic digestion and desorption solution, which is raw water 16.
  • the BOD was 2 O mg Z liter
  • the ammonia nitrogen concentration was 97 O mg Z liter
  • the BOD was 1 Z 10 or less with respect to the ammonia nitrogen.
  • the raw water 16 was supplied to the nitrification tank 1 via the raw water adjustment tank 2 and was subjected to nitrification treatment.
  • Table 2 shows the operating conditions for nitrification tank 1.
  • a biological carrier made of polyethylene glycol having a diameter of 5 mm was charged into the nitrification tank 1 at a volume of 10 vZv% of the apparatus volume, and continuous stirring was performed using a stirrer 15. Sludge was not returned to nitrification tank 1, and the SRT was set to one day.
  • the dissolved oxygen (DO) in the nitrification tank 1 was controlled to 1.5 to 2.5 mg / liter.
  • the blower 10 was operated when the dissolved oxygen became 1.5 mgZ liter or less, and stopped when the dissolved oxygen became 2.5 mg / liter or more. pH control was not actively performed.
  • the nitrification tank 1 is equipped with a pH meter, which is not shown in FIG.
  • the arithmetic and control unit 7 the N a OH solution using an alkali supply pump 13 and added pressure, was carried out by adding H 2 S 0 4 solution using acid feed pump 14 when it becomes equal to or greater than 350 OmgZ liters by. Consumption of Na OH in 20 ⁇ 100 gZ d, H 2 SO 4 was not consumed little.
  • Figure 5 shows changes in the quality of raw water and treated water.
  • Ammoniacal nitrogen in raw water was 780-930 mg Z liters, whereas ammoniacal nitrogen in treated water was 350-480 mgZl (430 mgZl on average) and nitrite nitrogen was 420-470 mg / liter. (On average, 46 Omg / liter), and the treatment was stable.
  • nitrate nitrogen is always less than 2 OmgZ liter.
  • the ratio of nitrite nitrogen to the total of nitrate nitrogen and nitrite nitrogen in the treated water is 98% or more.
  • the target nitrite nitrogen concentration was set at 45 Omg / liter, and the results were almost as planned.
  • the target nitrite nitrogen concentration was set to 450 mg / liter.
  • the addition of the alkali and the acid was determined by the pH of the nitrification tank 1, and the other operating conditions were the same as in Example 1.
  • H 2 SO 4 was added using a PH controller when the value became higher than the set value plus 0.2, and NaOH was added when the value became lower than the set value.
  • Table 3 shows the operating conditions and the quality (average value) of raw water and treated water. Table 3 Operating conditions and results of nitrification tank 1 (average value)
  • nitrite nitrogen in the treated water was 3 73MgZ liters.
  • H 2 S 0 4 raw M- alkalinity after the addition an average 5.2-fold goal nitrite nitrogen concentration, nitrite nitrogen concentration in the treated water is less than the target value (450 mg Bruno liters) Natsuta .
  • Example 3 In this example, the treatment was performed by an upward flow fluidized bed system as shown in FIG.
  • the biocarrier used in the transient method using the biocarrier in Fig. 1 and the biofilm filtration in Fig. 2 has a particle size of 3 to 5 mm.
  • the upward flow fluidized bed method uses a biological carrier with a small particle size of 0.1 to 0.5 mm, so the concentration of ammonia 'oxidizing bacteria in the nitrification tank increases. The rate of nitrite generation per nitrification tank was increased. For this reason, in the transient mode 0. 6k gZ - it had a (m 3. Bath d) is, in the upward-flow Doso scheme 3.
  • the processing was performed according to the flow shown in FIG.
  • the flow in Fig. 4 does not have a raw water adjustment tank, so the installation area can be smaller than that in the flow in Fig. 1.
  • the anaerobic digestion and desorption of sludge was treated according to the flow shown in FIG.
  • the capacity of the nitrification tank 1 is 100 liters.
  • the raw water used was the same as in Example 1, and the raw water M-alkalinity was set to 7 times the target nitrite nitrogen concentration so that the target nitrite nitrate concentration was 250 to 95 OmgZ liter.
  • Alkali or acid was added. Conditions other than the amounts of alkali and acid added were the same as in Example 1.
  • Table 4 shows the operating conditions and the quality of raw water and treated water (all average values).
  • Figure 6 shows the concentrations of ammonia nitrogen in raw water and ammonia nitrogen in treated water and nitrite nitrogen.
  • the nitrite nitrogen concentration of the treated water was 293 to 860 mg Z liter.
  • the nitrate concentration of the treated water was 15 mg / liter or less, and the ratio of nitrite nitrogen to the total of nitric nitrogen and nitrite nitrogen in the treated water was 95% or more.
  • Figure 7 shows the ratio of raw water M-alkalinity to the concentration of nitrite nitrogen in the treated water (raw water M-alkalinity Z concentration of the treated water nitrite nitrogen).
  • Figure 7 shows that the ratio of raw water M-alkalinity to nitrite nitrogen concentration was 6 to 8 times. This shows that the nitrite nitrogen concentration in the treated water can be controlled by adjusting the raw water M-alkalinity to 6 to 8 times the target nitrite nitrogen concentration.
  • the present invention is effective for wastewater containing ammonia nitrogen such as sewage, human waste, and industrial wastewater. Since nitrification can be performed efficiently, it is expected to be used in sewage treatment plants and various wastewater treatment facilities.

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  • Health & Medical Sciences (AREA)
  • Molecular Biology (AREA)
  • Biodiversity & Conservation Biology (AREA)
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  • Hydrology & Water Resources (AREA)
  • Engineering & Computer Science (AREA)
  • Environmental & Geological Engineering (AREA)
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  • Purification Treatments By Anaerobic Or Anaerobic And Aerobic Bacteria Or Animals (AREA)

Abstract

La présente invention a trait à un procédé pour le contrôle efficace de la concentration en azote sous forme de nitrite par la régulation de l'alcalinité M d'une eau non traitée contenant de l'azote ammoniacal, ainsi qu'à un appareil pour la mise en oeuvre du procédé. Le procédé permettant la nitrification d'eaux usées contenant de l'azote ammoniacal est caractérisé en ce qu'il comprend le contrôle de la concentration d'oxygène dissous dans un bassin de nitrification, la régulation de l'alcalinité M des eaux non traitées afin d'obtenir le nombre de fois de la concentration requise d'azote sous forme de nitrite, et la régulation du pH dans le bassin à une valeur dans une plage déterminée de sorte que l'azote ammoniacal contenu dans les eaux usées soit nitrifié en partie pour la régulation du rapport molaire de l'azote ammoniacal à l'azote sous forme de nitrite à une valeur déterminée. Il est préférable dans le procédé de nitrification des eaux usées que la quantité d'oxygène à fournir soit contrôlée de sorte que la quantité d'oxygène dissous dans le bassin de nitrification soit maintenue égale ou inférieure 3 mg/L et que le nombre de fois déterminé soit de 6 à 8 fois la concentration en azote sous forme de nitrite.
PCT/JP2004/014411 2003-09-25 2004-09-24 Procede et appareil pour la nitrification Ceased WO2005030654A1 (fr)

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JP2003333077 2003-09-25
JP2003-333077 2003-09-25

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Cited By (2)

* Cited by examiner, † Cited by third party
Publication number Priority date Publication date Assignee Title
WO2015177719A1 (fr) * 2014-05-21 2015-11-26 Imr Engineering & Technologies S.R.L. Installation et procédé de traitement des eaux usées
US20170217808A1 (en) * 2014-09-16 2017-08-03 Kurita Water Industries Ltd. Biological treatment method and biological treatment apparatus

Citations (4)

* Cited by examiner, † Cited by third party
Publication number Priority date Publication date Assignee Title
JPS6334798B2 (fr) * 1981-03-11 1988-07-12 Ebara Infilco
JPH05169091A (ja) * 1989-12-15 1993-07-09 Elf Atochem Sa 硝化用バイオマスの支持体、該支持体を用いて廃棄物の好気硝化を行う反応器及び生物学的方法、並びに窒素化合物の除去方法
JP7073714B2 (ja) * 2017-12-27 2022-05-24 株式会社リコー シート折り装置、画像形成システム
JP7115033B2 (ja) * 2018-05-24 2022-08-09 沖電気工業株式会社 現金処理装置

Patent Citations (4)

* Cited by examiner, † Cited by third party
Publication number Priority date Publication date Assignee Title
JPS6334798B2 (fr) * 1981-03-11 1988-07-12 Ebara Infilco
JPH05169091A (ja) * 1989-12-15 1993-07-09 Elf Atochem Sa 硝化用バイオマスの支持体、該支持体を用いて廃棄物の好気硝化を行う反応器及び生物学的方法、並びに窒素化合物の除去方法
JP7073714B2 (ja) * 2017-12-27 2022-05-24 株式会社リコー シート折り装置、画像形成システム
JP7115033B2 (ja) * 2018-05-24 2022-08-09 沖電気工業株式会社 現金処理装置

Cited By (2)

* Cited by examiner, † Cited by third party
Publication number Priority date Publication date Assignee Title
WO2015177719A1 (fr) * 2014-05-21 2015-11-26 Imr Engineering & Technologies S.R.L. Installation et procédé de traitement des eaux usées
US20170217808A1 (en) * 2014-09-16 2017-08-03 Kurita Water Industries Ltd. Biological treatment method and biological treatment apparatus

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