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    • 专利摘要:
    Procedure for the elimination of nitrogen by anaerobic pathways. The present invention relates to a process of partial anammox nitritation in biofilters in the main water line. (Machine-translation by Google Translate, not legally binding)
    公开号:ES2603858A2
    申请号:ES201531248
    申请日:2015-09-01
    公开日:2017-03-01
    发明作者:Mª Mar MICÓ RECHE；Carme PEREZ VIZUETE；Mª Caridad DONOSO FERNANDEZ；Carlos RODRÍGUEZ LÓPEZ
    申请人:Acciona Agua SA；
    IPC主号:
    专利说明:

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    PROCEDURE FOR THE ELIMINATION OF NITROGEN BY ROAD
    ANAEROBIAS
    DESCRIPTION
    The present invention relates to a process of partial anammox nitritation in biofilters in the main water line.
    STATE OF THE TECHNIQUE
    In recent years, the use of advanced processes that meet more sustainable requirements for the treatment of contaminated water has been considered. The increase in the demands on the quality of the purified water has caused that the treatment of these waters, and more specifically of the wastewater, includes not only the elimination of organic matter but also of nutrients such as phosphorus or nitrogen, associated with problems related to the eutrophication of the aquatic means that reproduce before the discharge to the natural channels of insufficiently treated waters.
    Particularly, this nitrogen removal can take place through different biological nitrite processes through which the ammoniacal nitrogen is bio-oxidized to nitrate, which is followed by the denitrification that ends up converting the nitrate into molecular nitrogen. This nitrification generally takes place in two stages. In the first of them, the ammonium-oxidizing bacteria (AOB) oxidize the ammonium to nitrite, while in the second stage, the nitrite-oxidants (NOB) end up generating the nitrates. On the other hand, during the process, reducing bacteria reduce nitrate to nitrite and this to N2.
    However, in the last decades an alternative is being imposed in which the oxidation of ammonium stops in nitrite, encouraging the presence of AOB bacteria against NOB, and the following reduction of nitrite to molecular nitrogen by denitrifying bacteria. By reducing the requirements of oxidation and reduction, this nitritation-denitrite system allows to reduce the energy needs by 25% compared to the conventional system, the required organic matter is also 40% lower, and a reduction of 30 % of the sludge generation.
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    Particularly, it highlights the special interest that the anammox process, acronym in English of anaerobic oxidation of ammonium, is recently awakening. In this process the bacteria of the Plactomycetes edge combine nitrite and ammonium to produce nitrogen gas under anoxic conditions (reduction of 50% of the oxygen consumption of a conventional denitrification) and without requiring organic matter (Liang, Z. et al. Bioresour Technol. 2011, 102, 710-715). The use of ammonia as an electron donor for the reduction of nitrite justifies the integration of partial nitritation, which produces the appropriate substrate for the subsequent anammox reaction (Fux, C. et al. Bioact. Subst. Bioremediation Technol. 2002, 99, 295-306). In this way, the elimination of nitrogen material is achieved in the same reactor or in two separate stages in series tanks, constituting a more sustainable and productive process by reducing energy consumption and, thanks to the bioelimination of nitrogen, would take place through intermediate species less harmful to the ozone layer.
    There is a bibliography of practical experiences in the use of these combined processes to eliminate nitrogen matter in real wastewater treatment plants. However, in most cases the process is applied in effluents with high ammonium load (<500 mgL-1) and high temperatures (> 30 ° C), as is the case of the digester's rejection or in industrial effluents from of anaerobic treatments that contain little or no organic load, conditions that do not reproduce in the main water line and that, in general, offer unfavorable conditions for the development of nitritating biomass and anammox biomass. On the one hand the temperature of this effluent ranges between 10 and 25 ° C, far from the optimum for the growth of anammox bacteria, favored at mesophilic temperatures, and which can also make it difficult to select oxidizing ammonium bacteria against oxidizing nitrite . On the other hand, the main line, having not been subjected to hydrolysis caused by biological processes of digestion of organic matter and being more diluted, contains low concentrations of ammonium, which is a particularly limiting condition in the case of anammox bacteria. Finally, the organic load of the main line is quite high compared to already digested effluents, which can be a problem of competition between autotrophic bacteria (AOB and anammox) and heterotrophs if the mass relationship between chemical oxygen demand (COD) and nitrogen is higher than unity, as well as a decrease in anammox activity.
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    Despite these limitations, there are advances that point to the viability of this new application of the partial nitrite / anammox process. To begin with, in relation to the organic load of the main effluent, some laboratory and pilot plant work already involves simultaneous processes of partial nitritation and anammox that are applied in simulated effluents with a chemical oxygen demand ratio (COD). English) versus 0.5 (g COD / g N) nitrogen, although at temperatures between 30-36 ° C. In the case of Winkler (Water Res., 2012, 46, 136-44), work was carried out at 20 ° C with effluents similar to the main sewage line, and elimination rates similar to previous works were obtained in which the effluent To treat was rich in ammonium. In the works of Kartal (Environ. Microbiol., 2007, 9, 635-642; FEMS Microbiol. Ecol., 2008, 63, 46-55) it is postulated that the organic matter present in these effluents is eliminated by the activity of bacteria Coexisting heterotrophs or certain anammox re-adapt their metabolism to use organic matter as an electron donor in the process of denitrification, a role that ammonium normally plays.
    Regarding the temperature-related problem, there are recent studies that indicate that with a gradual adaptation, the anammox bacteria can be operated under temperature conditions below the mesofflicas. It was even possible to achieve stability in a bioreactor in which the nitritation and anammox processes take place at 12 ° C (Hu et al., Appl. Environ. Microbiol., 2013, 79, 28072812).
    On the other hand, despite the low concentrations of ammonium that characterize the main line, there are studies that indicate that the nitrogen flow is perhaps more important than its concentration at the entrance. Thus, to achieve the adequate rate of nitrogen supply, it is required to apply short hydraulic residence times. It was demonstrated that the feasibility of working with low residence times obtaining high rates of nitrogen removal at 20-30 ° C and a low ammonium concentration of the input effluent (31-66 mgL-1). These studies seemed to conclude that lower specific anammox activity related to lower temperatures is not necessarily a problem, as long as biomass retention is sufficient. In addition, the negative effects that low HRT could cause on the retention of suspended biomass (Hendrickx et al., Water Res., 2012, 46, 21872193), could be mitigated with the use of reactors based on biofiltration technology.
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    Precisely biofilter-based systems offer support for the development of biofilms that allow greater retention despite working with high flow rates. The immobilization of microorganisms on a solid landfill achieves a high retention of biomass, which allows the process to be operated at higher flow rates and higher organic loads, and at the same time favor the development of slow-growing microorganisms.
    DESCRIPTION OF THE INVENTION
    Despite the advantages offered by the characteristics mentioned in the State of the Art, to house the development of anammox bacteria, highly sensitive to changes in the environment and extremely slow growth, there are only a few references to the use of biofilters such as anammox bioreactors referred to the treatment of effluents from the dairy and aquaculture industry.
    In the specific case of vertical flow bioreactors, similar to those proposed in the project, there are practical experiences on a laboratory scale in which the nitritation and anammox processes are carried out in the same reactor. However, the possibility that NOB bacteria, which can be developed to the detriment of AOB, also compete with the anammox for nitrites reinforces the need to separate the two processes into two different reactors, as proposed by the present invention.
    In a first aspect, the present invention relates to a water treatment process comprising the following steps:
    (a) optional biological treatment;
    (b) partial nitrite with ammonia-oxidizing bacteria from the water stream to be treated or the stream obtained in step (a) at a temperature between 14 and 28 ° C, and a pH between 6.7 and 8.6 ; Y
    (c) anaerobic oxidation of ammonia with anammox bacteria from the current obtained in step (b) in the main water line at a temperature between 14 and 28 ° C, and a pH between 7.0 and 8.6;
    characterized in that stages (b) and (c) take place in different reactors, and that the anammox bacteria used in stage (c) are deposited in expanded clay biofilters.
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    "Expanded clay" means a very light ceramic aggregate obtained from the expansion at high temperatures of special natural clays, characterized by a density comprised of the material ranging between 325 kg / m3 and 900 kg / m3. Preferably, the clays used have a density of between 750 to 900 kg / m3 and more preferably between 840 to 880 kg / m3.
    In a preferred embodiment, the water stream to be treated is subjected to a primary treatment, preferably decantation, where a phase composed of water is obtained, which has a total nitrogen concentration (NTK) of about 40-70 ppm, and another of organic material. Then the aqueous phase is subjected to a biological treatment, mainly to eliminate this organic matter. The NTK at the exit of this treatment is between 35-65 ppm.
    “Biological treatment” means any process used to eliminate organic matter, that is, aerobic processes of medium-load active sludge, biofiltration, biofilm processes with MBBR mobile supports, UASB anaerobic processes, anaerobic membrane reactors, etc.
    This provision allows the aeration required in biological treatment and in biofilter treatment to be less than that required with the conventional process.
    Next, the sludge generated in the biological treatment, together with the phase of organic matter obtained in the decanter of the primary treatment, are carried to the sludge line. From sludge dehydration a centrifugal drain is obtained having a nitrogen concentration of about 500 to 1100 ppm, the typical value being 1000 ppm (which is between 15-20% of all the nitrogen). That drain is taken to a reactor where partial nitritation with ammonium-oxidizing bacteria takes place and then to another different reactor that contains anammox bacteria. The effluent from this second tank, which has a nitrogen concentration of about 30 to 50 ppm, is taken to the biological treatment, along with the water obtained from the primary treatment.
    Therefore, in another preferred embodiment, the sludges obtained in the biological treatment are carried to the sludge line, and are treated following the following stages: (a) sludge dehydration;
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    (b) partial nitritation and anaerobic oxidation of ammonium from sludge dewatering, according to the conditions defined above.
    In another more preferred embodiment, the effluent from partial nitrite and anammox from sludge dewatering drains is recycled to the biological treatment of the main water line.
    Currently, we are working with a bed volume for anaerobic oxidation of ammonium calculated at 0.01195 m3, with flow rates of 15-16 l / h, which is giving elimination rates of 1.8-2.5 kg N elim / (m3bed d).
    These numbers, compared with those that the specialized bibliography used for the design of denitrification biofilters (WEF Manual of Practice No. 35, 2010), show the improvement that the anammox denitrification biofilters used in the present invention provide, exceeding the marked expectations by conventional denitrification biofilters, the technical limit of these having not been reached to date.
    As an additional advantage, between the cleaning periods, not only anammox biomass accumulates in the interstices of the clay material, a layer of about 3-6 cm thick of granular configuration mud, of marked color, also accumulates on the bed surface red-orange characteristic of the anammox biomass, which can be used for inoculation or bioaugmentation of other reactors that need this type of bacteria.
    Therefore, in another preferred embodiment, the bacteria from the anammox sludge tank tank are used for planting reactors where the reaction takes place the anaerobic oxidation stage of ammonia.
    Throughout the description and claims the word "comprises" and its variants are not intended to exclude other technical characteristics, additives, components or steps. For those skilled in the art, other objects, advantages and characteristics of the invention will be derived partly from the description and partly from the practice of the invention. The following example is provided by way of illustration, and is not intended to be limiting of the present invention.
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    EXAMPLES
    The invention will be illustrated below by tests carried out by the inventors, which shows the effectiveness of the product of the invention.
    Example 1.
    A flow of 10-16 l / h has been fed, in continuous, from a 1000 L tank, where the influent water is prepared periodically, using WWTP service water where the experimental installation is located, and adding the proportions of necessary salts (NH4Cl, NaNO2, NaHCO3), so that the influent water has the following characteristics.
    - Ammonium input: 30-40 mg N / l
    - Input nitrite: 35-49 mg N / l
    - Alkalinity 80-110 mg CaCO3 / l
    - pH: 7.00-7.60
    When using service water, the needs of other micronutrients that the process microbiology needs are covered.
    The biofilter fed is a pipe of polymeric material with the following dimensions:
    - Diameter: 0.13 m
    - Bed height: 0.90 m
    - Calculated area: 0,01327 m2
    - Calculated bed volume: = nr ^ h = n (0.13 / 2) 20.90 = 0.01195 m3
    The bed is a clay material (Filtralite® HC 2.5-5 and Filtralite® HR 4-8), where initially anammox bacteria released from an anammox biofilm from a digestion return water treatment system are inoculated. The inoculation consisted of the addition of about 5 liters of water with a concentration of about 2000-3000 mg / l of solids that contain mostly anammox family bacteria.
    After a period of acclimatization and distribution along the bed of clay material, an elimination of ammonium nitrite was observed more and more intense, maintaining that elimination a stoichiometric ratio (mg N-NO2 elim./mg N-NH4
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    elim.) in the usual environment of this process (1.0-1.4, being 1.3 on average), accompanied by the consequent appearance of nitrates (NO3-), also characteristic of this process.
    During certain periods of time related to the appearance of organic matter in the influent water, that is COD, lower amounts of nitrate than those expected by stoichiometry were measured, this fact being associated with the appearance of conventional denitrification processes.
    Once the anammox activity was detected, the experiment with a feed rate of around 10 l / h. This feeding was continued until the complete elimination of the substrates (ammonium and nitrite) was detected. This complete disappearance indicates that the capacity limit of the biofilter has not yet been reached, with which it was decided to increase the amount of influent water to look for this capacity limit.
    The load removed from the biofilters is calculated by dividing the amount of nitrogen removed over a day of operation, divided by the volume of the bed.
    In this way, at the beginning of the experiment, values of 1.2-1.3 kg N elim / (m3 bed) were achieved, reaching elimination rates of 1.8-2.0 kg N elim / (m3 bed) .d) with flow rates of 15-16 l / h.
    These filters with these loads need a backwash to eliminate the clogging every 4-5 days, operating at a surface load of about 1.1 m3 / m2 h, with which there is still room to increase their feeding.
    权利要求:
    Claims (5)
    [1]
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    1. Water treatment procedure comprising the following stages:
    (a) optional biological treatment;
    (b) partial nitrite with ammonia-oxidizing bacteria from the water stream to be treated or the stream obtained in step (a) at a temperature between 14 and 28 ° C, and a pH between 6.7 and 8.6 ; Y
    (c) anaerobic oxidation of ammonia with anammox bacteria from the current obtained in step () at a temperature between 14 and 28 ° C, and a pH between 7.0 and 8.6;
    characterized in that stages (b) and (c) take place in different reactors, and that the anammox bacteria used in stage (c) are deposited in expanded clay biofilters.
    [2]
    2. Method according to claim 1, wherein the biological treatment of step (a) is independently selected from the list comprising aerobic processes of medium-load active sludge, biofiltration, biofuel processes with MBBR mobile supports, UASB anaerobic processes, and anaerobic membrane reactors.
    [3]
    3. Procedure according to claim 2, wherein the sludge obtained in the biological treatment is carried to the sludge line and treated according to the following steps:
    (a) sludge dehydration;
    (b) Partial nitrite and anaerobic oxidation of ammonium from sludge dewatering, according to the conditions defined in claim 1, resulting in an effluent having a nitrogen concentration between 30 to 50 ppm.
    [4]
    4. Method according to claim 3, wherein the effluent resulting from step (b) is recirculated to the biological treatment defined in claim 2.
    [5]
    5. Method according to claim 3, wherein the bacteria from the anammox tank of the sludge line are used for planting reactors where stage (c) of claim 1 takes place.
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    同族专利:
    公开号 | 公开日
    ES2603858B1|2018-06-25|
    ES2603858R1|2017-08-09|
    引用文献:
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    CN108585389A|2018-07-12|2018-09-28|北京翰祺环境技术有限公司|A kind of charcoal load MBBR sewage disposal systems and sewage water treatment method|
    WO2021093215A1|2019-11-17|2021-05-20|凌志环保股份有限公司|Moving bed biofilm reactor coupled ammoxidation integrated purification tank|DE3434678C2|1984-08-11|1990-08-23|Hellmut Gunter 5063 Overath De Hofmann|
    GB2336359A|1998-04-14|1999-10-20|John Mowlem & Company Plc|Apparatus and method for wastewater treatment|
    US7082893B2|2003-04-03|2006-08-01|University Of Maryland Biotechnology Institute|Aquaculture nitrogen waste removal|
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