JPH0134678B2 - - Google Patents
Info
- Publication number
- JPH0134678B2 JPH0134678B2 JP29780685A JP29780685A JPH0134678B2 JP H0134678 B2 JPH0134678 B2 JP H0134678B2 JP 29780685 A JP29780685 A JP 29780685A JP 29780685 A JP29780685 A JP 29780685A JP H0134678 B2 JPH0134678 B2 JP H0134678B2
- Authority
- JP
- Japan
- Prior art keywords
- treatment
- wastewater
- organic
- biological
- denitrification
- 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.)
- Expired
Links
- 239000002351 wastewater Substances 0.000 claims description 35
- 239000010802 sludge Substances 0.000 claims description 20
- 239000005416 organic matter Substances 0.000 claims description 17
- 238000000034 method Methods 0.000 claims description 16
- 238000005273 aeration Methods 0.000 claims description 12
- 239000007788 liquid Substances 0.000 claims description 11
- XLYOFNOQVPJJNP-UHFFFAOYSA-N water Substances O XLYOFNOQVPJJNP-UHFFFAOYSA-N 0.000 claims description 11
- 238000000926 separation method Methods 0.000 claims description 9
- 229910052791 calcium Inorganic materials 0.000 claims description 8
- BVKZGUZCCUSVTD-UHFFFAOYSA-L Carbonate Chemical compound [O-]C([O-])=O BVKZGUZCCUSVTD-UHFFFAOYSA-L 0.000 claims description 7
- 238000000354 decomposition reaction Methods 0.000 claims description 7
- 150000007524 organic acids Chemical class 0.000 claims description 7
- 235000005985 organic acids Nutrition 0.000 claims description 2
- 239000000126 substance Substances 0.000 claims description 2
- 239000011575 calcium Substances 0.000 description 21
- IJGRMHOSHXDMSA-UHFFFAOYSA-N Atomic nitrogen Chemical compound N#N IJGRMHOSHXDMSA-UHFFFAOYSA-N 0.000 description 16
- 229910052757 nitrogen Inorganic materials 0.000 description 8
- QTBSBXVTEAMEQO-UHFFFAOYSA-N Acetic acid Natural products CC(O)=O QTBSBXVTEAMEQO-UHFFFAOYSA-N 0.000 description 5
- 206010042674 Swelling Diseases 0.000 description 4
- 238000006243 chemical reaction Methods 0.000 description 4
- 238000004090 dissolution Methods 0.000 description 4
- 150000003839 salts Chemical class 0.000 description 4
- 239000007787 solid Substances 0.000 description 4
- 230000008961 swelling Effects 0.000 description 4
- GRYLNZFGIOXLOG-UHFFFAOYSA-N Nitric acid Chemical compound O[N+]([O-])=O GRYLNZFGIOXLOG-UHFFFAOYSA-N 0.000 description 3
- 239000002253 acid Substances 0.000 description 3
- 238000007796 conventional method Methods 0.000 description 3
- 238000010586 diagram Methods 0.000 description 3
- 229910017604 nitric acid Inorganic materials 0.000 description 3
- 239000010865 sewage Substances 0.000 description 3
- 238000012360 testing method Methods 0.000 description 3
- 239000002699 waste material Substances 0.000 description 3
- MYMOFIZGZYHOMD-UHFFFAOYSA-N Dioxygen Chemical compound O=O MYMOFIZGZYHOMD-UHFFFAOYSA-N 0.000 description 2
- ZCCIPPOKBCJFDN-UHFFFAOYSA-N calcium nitrate Chemical compound [Ca+2].[O-][N+]([O-])=O.[O-][N+]([O-])=O ZCCIPPOKBCJFDN-UHFFFAOYSA-N 0.000 description 2
- 229910001882 dioxygen Inorganic materials 0.000 description 2
- 230000000694 effects Effects 0.000 description 2
- 230000005611 electricity Effects 0.000 description 2
- 125000000896 monocarboxylic acid group Chemical group 0.000 description 2
- 238000012545 processing Methods 0.000 description 2
- 238000003756 stirring Methods 0.000 description 2
- 239000006228 supernatant Substances 0.000 description 2
- 241000894006 Bacteria Species 0.000 description 1
- 229910002651 NO3 Inorganic materials 0.000 description 1
- 125000000218 acetic acid group Chemical group C(C)(=O)* 0.000 description 1
- QVGXLLKOCUKJST-UHFFFAOYSA-N atomic oxygen Chemical compound [O] QVGXLLKOCUKJST-UHFFFAOYSA-N 0.000 description 1
- 150000004649 carbonic acid derivatives Chemical class 0.000 description 1
- 239000000969 carrier Substances 0.000 description 1
- 241000902900 cellular organisms Species 0.000 description 1
- 238000010612 desalination reaction Methods 0.000 description 1
- 239000000852 hydrogen donor Substances 0.000 description 1
- XLYOFNOQVPJJNP-UHFFFAOYSA-M hydroxide Chemical compound [OH-] XLYOFNOQVPJJNP-UHFFFAOYSA-M 0.000 description 1
- 238000005259 measurement Methods 0.000 description 1
- 235000015097 nutrients Nutrition 0.000 description 1
- 230000033116 oxidation-reduction process Effects 0.000 description 1
- 239000001301 oxygen Substances 0.000 description 1
- 229910052760 oxygen Inorganic materials 0.000 description 1
- 239000002244 precipitate Substances 0.000 description 1
- 230000001105 regulatory effect Effects 0.000 description 1
- 238000004062 sedimentation Methods 0.000 description 1
- 239000013589 supplement Substances 0.000 description 1
- 238000004065 wastewater treatment Methods 0.000 description 1
Classifications
-
- 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
Landscapes
- Biological Treatment Of Waste Water (AREA)
- Treatment Of Biological Wastes In General (AREA)
- Activated Sludge Processes (AREA)
Description
（産業上の利用分野）
この発明は、下水等の一般有機物廃水や高濃度
有機物廃水を生物学的に浄化するのに利用される
有機質廃水の処理方法に関する。
（従来の技術とその問題点）
下水等の一般有機物廃水や有機酸廃水の浄化処
理には活性汚泥にて好気的条件下で有機物分解を
行つてBODを除去する生物処理が汎用されてい
る。
しかしながら上記の高負荷のBOD除去を行う
生物処理にあつては、酸素供給が律速となるた
め、活性汚泥の高濃度化をめざした高負荷運転に
は曝気速度の面より限界があり、また汚泥濃度が
高くなるとバルキング等の膨化現象が発生し易い
という問題があつた。因に上記曝気速度は高くて
も送気量として20〜40／m3・分程度、BOD除
去量２Kg／m3・日程度である。
（問題を解決するための手段）
この発明は、上記問題点を解決するためになさ
れたもので、有機物分解能力が極めて大きく、従
来に比較して処理設備の縮小ならびに電気消費量
の大幅な低減を可能とする有機質廃水の処理方法
を提供することを目的とする。
すなわちこの発明に係る有機質廃水の処理方法
は、有機物または有機酸を含有する廃水にNO3
態窒素を添加し、CaまたはMgの炭酸塩を生物キ
ヤリヤーとする活性汚泥により生物学的脱硝処理
して脱窒および有機物分解を行い、次いで曝気処
理によつて残余有機物の生物学的分解を行つたの
ち、固液分離にて処理水を上記生物キヤリヤーを
含む活性汚泥から分離することを特徴とするもの
である。
（発明の作用）
この発明においては、有機質廃水にNO3態窒
素を加えることにより、従来では好気的条件下の
生物処理にて行われていた有機物分解を生物学的
脱硝処理に転換する。すなわち、この脱硝処理に
おける有機物分解能力は上記好気的生物処理に比
較して非常に大きく、しかも活性汚泥（以下、
MLSSと称する）はCaまたはMgの炭酸塩を生物
キヤリヤーとしてその表面に高度に生物相を発達
させるのでMLSS濃度が高濃度に保持されること
から、高負荷運転によりBOD除去量が５〜６
Kg／ｍ・日という高効率の処理が可能であり、か
つMLSS沈降性が極めて良好であるため、バルキ
ング等の膨化現象が発生する惧れがなく固液分離
による処理水の抜き取りが非常に容易である。
この脱硝処理を行うために有機質廃水に添加さ
れるNO3態窒素源としては廃硝酸液あるいは
NO3 -イオンを含有する各種酸廃水をそのまま利
用できる。従つてこの発明方法では有機質廃水と
廃硝酸または他の酸廃水との併合処理が可能であ
る。
ここで、MLSSと生物キヤリヤーの炭酸塩は処
理条件下で長期間馴養して両者の濃度比が平衡に
達したものを使用する。この平衡時の濃度比は、
該炭酸塩と有機物の汚泥転化率によつて規制され
るが、例えば生物キヤリヤーがCaCO3、有機質
廃水が酢酸廃水、NO3態窒素源がHNO3である場
合、MLSS：CaCO3（重量比）≒１：10となるこ
とが判明している。この濃度比の場合、MLSSを
10000〜13000mg／にて運転する時、全固形分
（SS）は110000〜143000ml／ｇの濃度に達する
が、汚泥の膨化は全く観察されず、SVIが常に４
以下になることが判明しており、CaCO3が生物
キヤリヤーとして非常に有効に機能していること
が実証されている。
脱硝処理は、上記生物キヤリヤーに担持された
MLSSとNO3態窒素の存在下で有機質廃水を無分
子状酸素条件のもとに所要時間撹拌するだけで終
了する。この時、上記廃水中の有機物は脱窒菌に
対する水素供与体として分解消費される。なお、
添加されるNO3態窒素はの残留を避けるために
有機物に対する理論比よりも若干少な目に設定さ
れる。
しかして、残余の有機物は次の曝気処理によつ
て生物学的に分解されるが、その量が少ないこと
から曝気量は僅かで済む。
この曝気処理後に固液分離して得られる処理水
は、有機物がほぼ完全に分解されているので
BODが０に近く、かつ脱硝時に添加された窒素
分をほとんど含まず、しかもCaCO3の溶解度が
小さいために塩濃度が極めて少ないものとなつて
いる。
なお、この処理過程では当然のことながら
MLSSが増殖するので、このMLSSの増殖分を余
剰汚泥として除去する必要があるが、この余剰汚
泥中には生物キヤリヤーであるCaまたはMgの炭
酸塩が含まれる。そこで、取り出した余剰汚泥を
前記廃硝酸液ないしNO3 -イオンを有する酸廃水
中、あるいは処理対象が有機酸廃水である場合に
はこの廃水中に混合し、CaまたはMg分を可溶性
塩として溶解させて固液分離すれば、MLSSのみ
を除去できる。しかして上記可溶性塩は脱硝およ
び曝気時の生物学的分解作用で自動的に炭酸塩に
転化再生されて生物キヤリヤーとして機能する。
従つてCaまたはMg分は処理水中に溶解して逸失
する僅かな量を除いて再利用されることになり、
その補充はCaまたはMgの水酸化物等の形態で上
記逸失分に見合う量だけ上記の溶解工程で添加す
ればよい。
（実施例）
以下、この発明の実施例を第１図、第２図で示
す工程図に基づいて説明する。なお、以下におい
ては生物キヤリヤーとしてCaCO3を使用してい
るが、MgCO3でも差し支えない。
第１図の例では、余剰汚泥をNO3態窒素源で
あるHNO3廃水に混合してCa分をCa（NO3）2とし
て溶解している。この場合の反応は、
CaCO3＋2HNO3→Ca（NO3）2＋H2O＋CO2↑
で示され、CO2が発生する。またこの溶解工程で
は処理水に付随して逸失するCa分の補充のため
に少量のCa（OH）2を添加している。この反応は、
Ca（OH）2＋2HNO3→Ca（NO3）2＋2H2O
で示される。しかして上記溶解後に固液分離して
MLSSのみを固形分として分離除去している。
脱硝処理は上記固形分離後の分離液を有機質廃
水に添加し、CaCO3およびMLSSの存在下で無分
子状酸素条件（密閉）のもとに所要時間撹拌する
ことによつて行われ、脱窒と有機物分解が同時に
なされてN2およびCO2が発生すると共に、Ca
（NO3）2のCa分がCaCO3として析出する。処理対
象の有機質廃水は一般有機物廃水および有機酸廃
水のいずれでもよいが、例えば有機物が
CH3COOHである場合の反応は
５（CH3COO）2Ca＋8Ca（NO3）2
MLSS
―――――→
13CaCO3＋15H2O＋7CO2↑＋8N2↑
にて示される。
しかして脱硝工程で残存した少量の有機物は次
の曝気によつて生物学的に分解され、固形分は
CaCO3とMLSSのみとなり、続く固液分離にて非
常に良好に脱窒、脱塩されてBODもほぼ０とな
つた処理水が抜き出され、余剰汚泥は溶解工程へ
返送される。
第２図は余剰汚泥を処理対象の有機酸廃水に混
合してCa分を有機酸Ca塩として溶解し、HNO3
廃水はそのままの形で使用する例であり、他の処
理操作は第１図の場合と同様である。
（処理試験例）
有機質廃水として酢酸廃水を例にして処理効果
を次の条件で調べた。
＜生物処理槽＞
30×30×30cmの透明塩ビ製容器に天蓋、撹拌
機、散気管を付設したもので、有効容積は17。
＜原水＞
硝酸カルシウム〔Ca（NO3）2・4H2O、特級品〕
を純水に溶解してCa（NO3）2として132250ml／
の濃度とし、その340mlを分取してNO3 -に対す
る重量比が１：１となるCH3COOHおよび栄養
剤を加え、最後に純水を加えて全量を3400mlとし
た。
＜活性汚泥＞
下水処理場から入手したMLSSを用い、長期間
にわたつて馴養テストを行い、MLSSとCaCO3の
濃度が平衡（測定結果ではMLSS：CaCO3の重量
比＝１：10）に達したもの。
＜処理操作＞
活性汚泥（MLSS＋CaCO3）が沈降した生物処
理槽の上澄み液約4000mlを抜き取り、原水3400ml
を導入し、上記の抜き取つた上澄み液を加えるこ
とによつて全量を17とした。なお、MLSS濃度
は10000mg／である。続いて密閉下で撹拌機を
回転して脱硝処理を行つた後、曝気して好気的条
件として未分解の有機物を処理し、次いで静置し
て固液分離を行つた。以降、上記工程を処理サイ
クル24時間／日にて繰り返した。なお、上記脱硝
処理の終了時点は酸化還元電位の変化から検知し
たが、その結果から脱硝に要する時間は４〜６時
間であることが判明した。またSVIは常に４以下
であつた。
上記処理の結果を表１に示す。また各処理サイ
クルでのNO3 -濃度、NO2 -、BOD、COD、酸化
還元電位（ORP）の経時変化の平均値を第３図
に示す。なお第３図中ｔは曝気開示時点である。
(Field of Industrial Application) The present invention relates to a method for treating organic wastewater that is used to biologically purify general organic wastewater such as sewage or highly concentrated organic wastewater. (Conventional technology and its problems) Biological treatment, which removes BOD by decomposing organic matter using activated sludge under aerobic conditions, is commonly used to purify general organic wastewater such as sewage and organic acid wastewater. . However, in the case of the above-mentioned biological treatment that performs high-load BOD removal, oxygen supply is rate-limiting, so there is a limit to high-load operation aimed at increasing the concentration of activated sludge due to the aeration rate. There was a problem that when the concentration became high, swelling phenomena such as bulking were likely to occur. Incidentally, even if the aeration rate is high, the amount of air supplied is about 20 to 40/m 3 ·min, and the amount of BOD removed is about 2 kg/m 3 ·day. (Means for Solving the Problems) This invention was made to solve the above problems, and has an extremely high ability to decompose organic matter, reducing processing equipment and significantly reducing electricity consumption compared to conventional methods. The purpose of the present invention is to provide a method for treating organic wastewater that enables the treatment of organic wastewater. That is, the method for treating organic wastewater according to the present invention is to treat wastewater containing organic substances or organic acids with NO 3
Denitrification and organic matter decomposition are carried out through biological denitrification using activated sludge using Ca or Mg carbonate as a biological carrier, and then biological decomposition of residual organic matter is carried out through aeration treatment. After that, the treated water is separated from the activated sludge containing the biological carrier by solid-liquid separation. (Operation of the invention) In the present invention, by adding NO 3 nitrogen to organic wastewater, organic matter decomposition, which was conventionally performed by biological treatment under aerobic conditions, is converted to biological denitrification treatment. In other words, the ability to decompose organic matter in this denitrification treatment is much greater than that in the aerobic biological treatment, and in addition, activated sludge (hereinafter referred to as
(referred to as MLSS) uses Ca or Mg carbonate as a biological carrier and develops a highly biota on its surface, so the MLSS concentration is maintained at a high concentration, so the amount of BOD removed can be reduced to 5 to 6 by high-load operation.
Highly efficient treatment of kg/m/day is possible, and the MLSS sedimentation property is extremely good, so there is no risk of swelling phenomena such as bulking occurring, and it is very easy to extract the treated water by solid-liquid separation. It is. The NO 3 nitrogen source added to organic wastewater for this denitrification process is waste nitric acid solution or
Various acid wastewaters containing NO 3 -ions can be used as is. Therefore, the method of the present invention allows the combined treatment of organic wastewater and waste nitric acid or other acid wastewater. Here, the MLSS and the carbonate of the biological carrier are used which have been acclimatized for a long period of time under the treatment conditions and whose concentration ratio has reached an equilibrium. The concentration ratio at equilibrium is
It is regulated by the carbonate and organic sludge conversion rate, but for example, when the biological carrier is CaCO 3 , the organic wastewater is acetic acid wastewater, and the NO 3 nitrogen source is HNO 3 , MLSS: CaCO 3 (weight ratio) It has been found that the ratio is approximately 1:10. For this concentration ratio, the MLSS is
When operating at 10000~13000mg/g, the total solid content (SS) reaches a concentration of 110000~143000ml/g, but no sludge swelling is observed and SVI is always 4.
It has been found that CaCO 3 functions very effectively as a biological carrier. The denitrification process was carried out on the above biological carrier.
Simply stir organic wastewater under non-molecular oxygen conditions for the required time in the presence of MLSS and NO 3- state nitrogen. At this time, the organic matter in the wastewater is decomposed and consumed as a hydrogen donor for denitrifying bacteria. In addition,
The added NO 3 nitrogen is set to be slightly lower than the theoretical ratio to the organic matter in order to avoid residual NO. Although the remaining organic matter is biologically decomposed by the subsequent aeration treatment, the amount of aeration is small because the amount is small. The treated water obtained by solid-liquid separation after this aeration treatment has almost completely decomposed organic matter.
The BOD is close to 0, it contains almost no nitrogen added during denitrification, and the solubility of CaCO 3 is low, so the salt concentration is extremely low. In addition, in this processing process, of course
Since MLSS proliferates, it is necessary to remove the proliferated MLSS as surplus sludge, and this surplus sludge contains carbonate of Ca or Mg, which is a biological carrier. Therefore, the extracted excess sludge is mixed with the waste nitric acid solution or acid wastewater containing NO 3 - ions, or into this wastewater if the target to be treated is organic acid wastewater, and the Ca or Mg content is dissolved as a soluble salt. Only MLSS can be removed by solid-liquid separation. The above-mentioned soluble salts are automatically converted and regenerated into carbonates by biological decomposition during denitrification and aeration, and function as biological carriers.
Therefore, the Ca or Mg content will be reused except for a small amount that is dissolved and lost in the treated water.
The supplement may be added in the form of Ca or Mg hydroxide in an amount corresponding to the lost amount during the dissolution step. (Example) Hereinafter, an example of the present invention will be described based on process diagrams shown in FIGS. 1 and 2. Although CaCO 3 is used as the biological carrier in the following, MgCO 3 may also be used. In the example shown in FIG. 1, excess sludge is mixed with HNO 3 wastewater, which is a NO 3 nitrogen source, and Ca content is dissolved as Ca(NO 3 ) 2 . The reaction in this case is shown as CaCO 3 +2HNO 3 →Ca(NO 3 ) 2 +H 2 O+CO 2 ↑, and CO 2 is generated. In addition, in this dissolution process, a small amount of Ca(OH) 2 is added to replenish the Ca that is lost along with the treated water. This reaction is shown as Ca(OH) 2 + 2HNO 3 →Ca(NO 3 ) 2 + 2H 2 O. However, after the above dissolution, solid-liquid separation
Only MLSS is separated and removed as a solid component. Denitrification treatment is performed by adding the separated liquid after the solid separation described above to organic wastewater and stirring for the required time under non-molecular oxygen conditions (closed) in the presence of CaCO 3 and MLSS. and organic matter decomposition at the same time, producing N 2 and CO 2 , as well as Ca
The Ca component of (NO 3 ) 2 precipitates as CaCO 3 . The organic wastewater to be treated may be general organic wastewater or organic acid wastewater, but for example, if organic wastewater is
The reaction in the case of CH 3 COOH is shown as 5(CH 3 COO) 2 Ca + 8Ca (NO 3 ) 2 MLSS ――――――→ 13CaCO 3 +15H 2 O + 7CO 2 ↑+8N 2 ↑. However, the small amount of organic matter remaining in the denitrification process is biologically decomposed by the next aeration process, and the solid content is reduced.
The treated water, which contains only CaCO 3 and MLSS, is very well denitrified and desalted in the subsequent solid-liquid separation, and the BOD is almost 0, and the excess sludge is returned to the dissolution process. Figure 2 shows that surplus sludge is mixed with organic acid wastewater to be treated, Ca content is dissolved as organic acid Ca salt, and HNO 3
This is an example in which wastewater is used as it is, and other treatment operations are the same as in the case of FIG. (Treatment test example) Using acetic acid wastewater as an example of organic wastewater, the treatment effect was investigated under the following conditions. <Biological treatment tank> A 30 x 30 x 30 cm transparent PVC container equipped with a canopy, a stirrer, and an aeration pipe, with an effective volume of 17 cm. <Raw water> Calcium nitrate [Ca (NO 3 ) 2・4H 2 O, special grade]
Dissolved in pure water to obtain 132,250ml of Ca( NO3 ) 2 /
A concentration of 340 ml was taken out, CH 3 COOH and nutrients were added at a weight ratio of 1:1 to NO 3 - , and finally pure water was added to bring the total volume to 3400 ml. <Activated sludge> Using MLSS obtained from a sewage treatment plant, an acclimatization test was conducted over a long period of time, and the concentration of MLSS and CaCO 3 reached equilibrium (in the measurement results, the weight ratio of MLSS:CaCO 3 = 1:10). What I did. <Treatment operation> Approximately 4,000 ml of supernatant liquid from the biological treatment tank in which activated sludge (MLSS + CaCO 3 ) has settled is extracted, and 3,400 ml of raw water is extracted.
was introduced, and the total volume was made up to 17 by adding the supernatant liquid extracted above. Note that the MLSS concentration is 10000 mg/. Subsequently, a stirrer was rotated under sealed conditions to perform denitrification treatment, followed by aeration to treat undecomposed organic matter under aerobic conditions, and then left to stand to perform solid-liquid separation. Thereafter, the above steps were repeated at a treatment cycle of 24 hours/day. The end point of the denitrification process was detected from the change in the oxidation-reduction potential, and the results revealed that the time required for denitrification was 4 to 6 hours. In addition, SVI was always below 4. The results of the above treatment are shown in Table 1. Furthermore, the average values of the changes over time in NO 3 - concentration, NO 2 - , BOD, COD, and redox potential (ORP) in each treatment cycle are shown in FIG. Note that t in FIG. 3 is the time point at which aeration starts.
【表】
（発明の効果）
この発明の処理方法は、有機質廃水にNO3態
窒素を添加してCaまたはMgの炭酸塩を生物キヤ
リヤーとする活性汚泥の存在下で生物学的脱硝処
理を行うものであり、活性汚泥が高濃度に保持さ
れて有機物の高負荷運転が可能であつて、脱硝時
の有機物分解能力が極めて大きいため、従来にお
いてこの種廃水に適用されていた好気的条件下で
の生物処理を上記脱硝処理に転換してかつ従来よ
りも格段に優れた処理効率を達成でき、また従来
に比較して設備の縮小および消費電気量の大幅な
低減が可能であり、しかもバルキング等の膨化現
象を発生する惧れがなく、脱窒、脱塩も良好にな
される。[Table] (Effects of the Invention) The treatment method of the present invention involves adding NO 3 nitrogen to organic wastewater and performing biological denitrification treatment in the presence of activated sludge using Ca or Mg carbonate as a biological carrier. The activated sludge can be maintained at a high concentration, making it possible to operate under a high load of organic matter, and the ability to decompose organic matter during denitrification is extremely high, making it possible to maintain the activated sludge under the aerobic conditions conventionally applied to this type of wastewater. It is possible to convert the biological treatment in the above to the denitrification treatment described above, and achieve much higher treatment efficiency than conventional methods.In addition, compared to conventional methods, it is possible to downsize the equipment and significantly reduce the amount of electricity consumed. There is no risk of swelling phenomena such as these occurring, and denitrification and desalination can be performed well.
第１図および第２図はこの発明に係る廃水処理
方法の実施例を示す工程図、第３図は処理試験例
における各種処理指標の経時変化を示す特性図で
ある。
FIGS. 1 and 2 are process diagrams showing an example of the wastewater treatment method according to the present invention, and FIG. 3 is a characteristic diagram showing changes over time in various treatment indicators in treatment test examples.
Claims (1)
態窒素を添加し、CaまたはMgの炭酸塩を生物キ
ヤリヤーとする活性汚泥により生物学的脱硝処理
して脱窒および有機物分解を行い、次いで曝気処
理によつて残余有機物の生物学的分解を行つたの
ち、固液分離にて処理水を上記生物キヤリヤーを
含む活性汚泥から分離することを特徴とする有機
質廃水の処理方法。1 NO 3 to wastewater containing organic substances or organic acids
Denitrification and organic matter decomposition are carried out through biological denitrification using activated sludge using Ca or Mg carbonate as a biological carrier, and then biological decomposition of residual organic matter is carried out through aeration treatment. A method for treating organic wastewater, which comprises separating the treated water from the activated sludge containing the biological carrier by solid-liquid separation.
Priority Applications (1)
| Application Number | Priority Date | Filing Date | Title |
|---|---|---|---|
| JP60297806A JPS62152593A (en) | 1985-12-25 | 1985-12-25 | Treatment of organic waste water |
Applications Claiming Priority (1)
| Application Number | Priority Date | Filing Date | Title |
|---|---|---|---|
| JP60297806A JPS62152593A (en) | 1985-12-25 | 1985-12-25 | Treatment of organic waste water |
Publications (2)
| Publication Number | Publication Date |
|---|---|
| JPS62152593A JPS62152593A (en) | 1987-07-07 |
| JPH0134678B2 true JPH0134678B2 (en) | 1989-07-20 |
Family
ID=17851407
Family Applications (1)
| Application Number | Title | Priority Date | Filing Date |
|---|---|---|---|
| JP60297806A Granted JPS62152593A (en) | 1985-12-25 | 1985-12-25 | Treatment of organic waste water |
Country Status (1)
| Country | Link |
|---|---|
| JP (1) | JPS62152593A (en) |
Families Citing this family (3)
| Publication number | Priority date | Publication date | Assignee | Title |
|---|---|---|---|---|
| FR2738234B1 (en) * | 1995-08-29 | 1998-10-30 | Degremont | PROCESS FOR REMOVAL OF NITROGEN COMPOUNDS AND REMINERALIZATION OF LOWLY MINERALIZED WATER |
| CN111348752A (en) * | 2018-12-21 | 2020-06-30 | 中国石油化工股份有限公司 | Treatment method of high-salt degradation-resistant wastewater |
| CN114262066A (en) * | 2021-12-23 | 2022-04-01 | 西安建筑科技大学 | Method and reactor for simultaneous removal of organic matter by microorganism-induced calcium precipitation |
-
1985
- 1985-12-25 JP JP60297806A patent/JPS62152593A/en active Granted
Also Published As
| Publication number | Publication date |
|---|---|
| JPS62152593A (en) | 1987-07-07 |
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