3.1
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Performance of MPDRs for nitrate-containing water treatmentFive reactors were continuously operated for 137 days to investigate the interaction between different mZVI-carbon ratios and denitrification performance (Fig. 1a), and the operational phase was divided into three stages with HRT, influent NO3&#; concentration and additional carbon source as variables (Table 1). In each stage, the denitrification reactors demonstrated a certain potential for NO3&#;-N removal. In general, 2-MPDR showed a consistent and effective performance in denitrification capacity under various operating conditions. During the whole experimental period, 2-MPDR achieved a maximum NO3&#;-N removal efficiency of 97.6&#;±&#;1.3% and a maximum denitrification load of 79.68&#;±&#;1.92 g N (m3 d)&#;1, achieving a basic removal of NO3&#;. The NO3&#;-N removal efficiency in four reactors ( not including C-MPDR) decreased with the shortening of hydraulic retention time (HRT) in stage 1, but the denitrification load continued to increase as a response to more frequent interactions. In stage 2 (from day 48&#;89), the differences in denitrification performance between individual denitrification reactors increased as the influent NO3&#; concentration increased. C-MPDR presented an enhanced denitrification potential under high NO3&#;-N concentration influent conditions, and this effect can be attributed to the absorption capacity of AC for NO3&#;. Subsequently, COD at 10, 20 and 40 mg L&#;1 was introduced into the denitrification reactors in stage 3 (from day 96&#;137) to investigate the potential impact of carbon sources on the heterotrophic denitrification pathway. The introduction of methanol assisted each denitrification reactor in reducing NO3&#;-N, demonstrating the potential for heterotrophic denitrification in each denitrification reactor. Unexpectedly, the effluent NO3&#; of M-MPDR was not significantly reduced in response to the addition of methanol. In any case, the denitrification capacity of M-MPDR was lower than that of other reactors except C-MPDR in all reaction stages.
Fig. 1Performance of denitrification reactors during the continuous operation (stages 1&#;3). a The influent NO3&#;-N; the effluent NO3&#;-N of C-MPDR, 1-MPDR, 2-MPDR, M-MPDR and V-MPDR; b NH4+-N concentration, NO2&#;-N concentration, NO3&#;-N removal loads, NO3&#;-N removal efficiency and NH4+ generation rate in 2-MPDR in entire test stage (0&#;137 d)
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In addition, CMC produced by AC enabled 2-MPDR in enhancing the average denitrification rate by 8.4% relative to V-MPDR (P&#;=&#;0.057). The enhanced denitrification performance of 2-MPDR could be linked to the acid modification, which is likely to facilitate the electron transfer process between NO3&#; and mZVI. And the oxidation rate of mZVI has been established as the rate-limiting factor for the chemical denitrification pathway. 2-MPDR demonstrated a greater NO3&#;-N removal capacity than 1-MPDR in both stages 1 and 2, which provides strong evidence that CMC performed the most effective NO3&#;-N removal at a 2:1 ratio of mZVI to carbon. Without mZVI, C-MPDR demonstrated a nominal denitrification capacity in stages 1 and 2, and this further suggests that multipathway denitrification primarily occurred in the presence of mZVI.
With the observation of nitrogen form transformation in 2-MPDR (Fig. 1b), we found the hybrid denitrification process combined chemical and biological denitrification in the denitrification reactors. In stage 1, NH4+-N concentration decreased from the highest 2.53&#;±&#;0.26 mg L&#;1 to 0.71&#;±&#;0.09 mg L&#;1 as HRT dropped from 24 to 12 h and 6 h. Simultaneously, higher rates of NH4+ production were observed at longer HRT, implying that the chemical denitrification reaction requires at least 12 h for sufficient interaction. Moreover, a significant increase in effluent NH4+-N concentration was attributed to the increase in influent NO3&#;-N concentration in stage 2. This result was assigned to the promotion of reaction &#; and &#; (Additional file 1: Text S4), as the increase in NO3&#; concentration enhanced the frequency of collisions between mZVI and NO3&#; ions. We found that the concentration of NO2&#;-N in M-MPDR was much higher than in other reactors throughout the whole stages (Additional file 1: Fig. S1). This result indicated that the pronounced reaction occurring in M-MPDR was chemical denitrification involving reaction &#; (Additional file 1: Text S4). Interestingly, we observed a lower effluent concentration of NO2&#;-N in 2-MPDR than in M-MPDR, while 2-MPDR exhibited higher NO3&#;-N removal, suggesting the presence of the microbial-induced biological denitrification pathway. Since M-MPDR effluent had the highest concentrations of NO2&#;-N, it is puzzling that M-MPDR employing only mZVI resulted in such a low NO3&#;-N removal rate. At the start of the experiment, we anticipated that AC only performed an auxiliary role, while mZVI was the predominant reactant for multipathway denitrification. It is speculated that AC could provide an abundant pore structure for microbial growth and metabolism while promoting the rate of mZVI oxidation, and the abundant elements on the surface of AC also supported the growth of related denitrifying bacteria. In the SEM&#;EDS assay, a variety of elements such as phosphorus (P) and nitrogen (N) were detected on the surface of AC (Additional file 1: Fig. S2).
3.2
Observation on the surface of CMC in different MPDRsSEM analysis was performed after stage 3&#;3 to visualize the microstructures of CMC, and the bacteria occurrence in the biofilms. Figure 2 illustrates the adhesive's (phenolic resin) porous microstructure of CMC. Given that both iron and carbon materials have smooth surfaces, the porous microstructure of CMC could extend to a larger area based on iron and carbon, which could be conducive to providing more sites for the proliferation of denitrifying bacteria. The microstructure of mZVI surface was rough and strongly weathered, and microbes in the biofilm were observed to colonize the mZVI surface (red dashed line) (Fig. 2B). The irregular structure could effectively alleviate the passivation of Fe by reducing the exposed area, thus allowing the continuous oxidation of mZVI and the transfer of electrons. Additionly, the relative content of oxygen (O) element on the CMC surface in 2-MPDR was significantly higher than that in V-MPDR, while the amounts of Fe and C were relatively reduced (Additional file 1: Fig. S2).
Fig. 2Characterization of CMC in denitrification reactors following the long-term experiment. Visualization of biochar surface (A), mZVI surface (B) and adhesive surface (C); XRD patterns D of CMC in M-MPDR, 2-MPDR and C-MPDR
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Although it was observed that Fe transferred electrons to NO3&#; in the reactors and promoted inefficient denitrification by AC, the mineral species formed by the oxidation of mZVI on the CMC surface in different reactors was unclear at the end of the experiment. XRD patterns confirmed that the presence of AC promoted the generation of goethite on the CMC surface in 2-MPDR. The diffraction peaks at 2θ values of 26.2° (002) and 42.8° (100) revealed the graphitized properties of carbon after denitrification in C-MPDR (Mitravinda et al. ). For M-MPDR, three diffraction peaks occurred at around 44.7° (110), 65.0° (200), and 82.3° (211) corresponding to the α-Fe crystalline phase. The diffraction peaks of Fe were still detectable throughout the experiment. This suggests the incomplete reaction of mZVI in M-MPDR within the experimental period. In addition, diffraction peaks representing carbon at 2θ values of 26.6° and goethite (α-FeOOH) at 2θ values of 21.2° (101) and 36.6° (021) were detected on the surface of 2-MPDR. Goethite was the primary product of the multipathway denitrification, deposited on the surface of mZVI, and was observed in Fe0 corrosion progression elsewhere (Yang et al. ; Li et al. ). Fe3O4 as an iron mineral with excellent electron transfer capacity was not observed in denitrification reactors, which was attributed to the specific environmental elements (high pH and low ORP) necessary for Fe3O4 generation (Chen et al. ), while the pH in 2-MPDR remained around 7.8 throughout the experiment. It is known that the precipitation of goethite on the CMC surface can potentially inhibit the continued oxidation of mZVI. Furthermore, the oxidation process of carbon and mineral intercalation could form a biochar-mineral composite layer on the surface, and this effect could result in greater resistance to chemical oxidation (Wang et al. a). The obvious Fe-carbon composite layer was not observed in this study, thus indicating that the rate of mZVI oxidation was not limited in 2-MPDR.
3.3
Contribution ratios of denitrification in different pathways in 2-MPDRAnalysis of long-term experiments confirmed the pronounced chemical denitrification process in MPDRs, while the bio-denitrification pathway could also be involved in the NO3&#; removal process, but the contribution of individual pathway remains unclear. The denitrification contribution ratios test was performed to determine the proportion of different denitrification pathways in NO3&#;-N removal in 2-MPDR. AD and HD (exogenous NaHCO3, methanol) differed in the initial NO3&#;-N concentration since the added microbial inoculum contained a small amount of nitrogen. The result in CD group indicated a significant correlation between the NO3&#;-N removal rate and the mass of CMC addition (P&#;<&#;0.01). CD-6 exhibited a greater NO3&#;-N removal efficiency of 81.9% with maximum CMC addition, but it was slightly lower than the 91.5% removal efficiency in HD but higher than the 76.7% removal efficiency in AD (Fig. 3a). The results indicated that the chemical denitrification was more pronounced than biological denitrification in the initial experimental period. Low concentrations of NH4+-N and NO2&#;-N accumulated in HD and AD before the test, with the NO2&#;-N concentration decreasing slowly throughout the test (Fig. 3b). NH4+-N accumulated in the first 10 min, but decreased in the subsequent 230 min. This trend further proved the dominant role of chemical denitrification in the early stage of the reaction. The addition of microorganisms increased the average concentrations of Fe (Fe2+ and Fe3+) in reaction systems (Additional file 1: Fig. S3a), which could be attributed to the facilitated dissolution of mZVI by the secretion of denitrifying microorganisms.
Fig. 3Contributions of chemical, heterotrophic and autotrophic denitrification in 2-MPDR. a Variation of NH4+-N concentrations in CD, AD and HD; b Variation of NO2&#;-N, NH4+-N concentrations in AD and HD
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The addition of CMC in CD was fitted to the NO3&#;-N removal rate as a linear fitting equation for calculating the contributions of chemical denitrification reactions in AD and HD (Additional file 1: Fig. S3b). NO3&#;-N removal was calculated based on the average NO3&#;-N concentration at 240 min HRT (7.01 mg L&#;1 in AD and 2.46 mg L&#;1 in HD). The average removal of NO3&#;-N in AD and HD was calculated to be 48.47 and 45.64 g N (m3 d)&#;1, respectively. Based on the linear fitting equation of the chemical denitrification rate in CD, the contributions of autotrophic denitrification pathway in AD and heterotrophic denitrification pathway in HD were calculated to be 19. 58 and 14.45 g N (m3 d)&#;1. The result showed that chemical, autotrophic and heterotrophic denitrification accounted for 57.3%, 24.6% and 18.1% of the total denitrification, respectively. However, autotrophic denitrification (84.1%) occupied a greater share compared to heterotrophic denitrification (18.9%) in similar reported iron-carbon reactors (Deng et al. ). Although heterotrophic denitrification was thermodynamically superior to autotrophic denitrification (Rezania et al. ), autotrophic denitrification was observed as the more dominant bio-denitrification pathway in this study.
3.4
Determination and variance analysis of microbial communities in MPDRsLimited by the reaction time and hydraulic conditions in denitrification reactors, the acidification of biochar had no significant contribution to the denitrification capacity of denitrification reactors, while increasing the ratio of mZVI to carbon in CMC remarkably reduced the NO3&#;-N effluent concentration in these long-term trials. Therefore, it is necessary to ascertain the impact of AC and ratios of mZVI to carbon on community structures and the variations of autotrophic and heterotrophic denitrification populations in each reactor through microbial and enzyme activity analysis. The dominant species of the genus in denitrification reactors were successively Acidovorax, Azoarcus and Limnobacter, all of which belong to the phylum Proteobacteria (Fig. 4). Proteobacteria were the predominant microbial phylum in denitrification reactors and were also identified as the phylum of most denitrifying bacteria widely existing in sewage treatment plants (Additional file 1: Fig. S4) (Chen et al. ). Acidovorax, which belongs to the phylum of Proteobacteria, is widely recognized as dominant mixotrophic denitrifying bacteria (Shen et al. ; Jiang et al. ). The majority of species in the genus Azoarcus could reduce NO3&#; and NO2&#; (Myung et al. ). It is noteworthy that this genus was found mainly in numerous bio-electrochemical studies (Shehab et al. ; Mei et al. ), while the application of electrodes to enhance electron transfer shares a certain degree of similarity with mZVI-carbon micro-electrolytic galvanic cells. Previous studies have demonstrated that Limnobacter was the heterotrophic denitrifying bacteria with the ability to reduce NO3&#; and NO2&#;(Wang et al. b). Additionally, Denitratisoma and Thauera are both well-known relevant denitrifying bacteria, both of which were significantly dispersed in 2-MPDR (10.22% and 5.07%, respectively) and V-MPDR (6.96% and 1.46%, respectively) (Wang et al. b). By accounting for the relative abundance of autotrophic and denitrification-related genera, it was revealed that the average percentage of autotrophic denitrifying bacteria increased from 1.2% to 5.6% with the application of AC than virgin carbon. The above results suggest that AC could further promote the growth of autotrophic denitrifying bacteria and assist the expansion of the dominance ascribed to autotrophic denitrifying bacteria. This effect may originate from the acceleration of electron transfer related to mZVI. It is worth noting that according to α-diversity analysis (Shannon and Simpson index), microorganisms in M-MPDR manifested the greatest diversity and absolute abundance, while the lowest microbial abundance was found in 1-MPDR and 2-MPDR utilizing AC (Fig. 4a). Samples from M-MPDR did not cluster significantly in the principal component analysis (PCA), revealing a greater bacterial species abundance (Additional file 1: Fig. S5). It was consistent with the α-diversity analysis (Fig. 4a) and disclosed the most significant differences in microbial community composition between M-MPDR and other denitrification reactors. Simultaneously, the samples from 2-MPDR and V-MPDR were clustered closely along PCA 2 axis, indicating a shared majority microbial community composition across both systems.
Fig. 4a Relative abundance of microbial composition at the genus level in denitrification reactors; b Relative abundance of functional genes encoding for NR, NAR, NIR, NCR and NOR in 2-MPDR and V-MPDR; c Relative abundance of functional genes encoding for NAD(P)H dehydrogenase, ubiquinone, riboflavin and iron acceptor protein in reactors
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Moreover, it was observed that the relative abundance of Thermomonas and Thauera was higher in 2-MPDR (0.23% and 5.07%) compared to V-MPDR (0.06% and 1.46%). In previous studies, Thermomonas and Thauera were identified to be efficient in removing NO3&#; using hydrogen as an electron donor (Wang et al. ; Shi et al. ). The NO3&#;-dependent genera Azospira (1.94%) and Pseudomonas (1.47%), known as denitrifying bacteria, were also detected exclusively in the biofilm of 2-MPDR (Zhang et al. ). Notably, Comamonadaceae, identified to use NO2&#; for anaerobic respiration (Yang et al. ), was observed with the highest relative abundance (3.30%) in V-MPDR. In contrast, this dominant bacterium was not detected in M-MPDR, which also had NO2&#;-N accumulation in long-term trials. This result was attributed to the absence of NO2&#; conversion pathway in M-MPDR, which took chemical denitrification as the main denitrification reaction.
Based on the above analysis, the relative abundance of denitrification functional genes was associated with the denitrification capacity of denitrification reactors by encoding denitrification functional enzymes. The relative abundance of denitrification functional genes encoding NO3&#; and NO2&#; reductase (NR), nitrate reductase (NAR), nitrite reductase (NIR), nitric oxide reductase (NCR), and nitrous oxide reductase (NOR) were observed to be highest in 2-MPDR (Fig. 4b). All of these functional genes showed a synergistic effect in catalyzing the reduction of NO3&#; to N2(Chen et al. ), thereby contributing to the denitrification process. Additional file 1: Fig. S4 illustrates that the relative abundance of relevant denitrification functional genes in different reactors was ranked as 2-MPDR&#;>&#;V-MPDR&#;>&#;1-MPDR&#;>&#;M-MPDR&#;>&#;C-MPDR. Thus, in the presence of mZVI, carbon has been shown to affect the bio-denitrification system, while AC could further promote microbial activity in bio-denitrification. It is worth noting that the gene encoding iron complex receptor protein was significantly expressed in 2-MPDR (Fig. 4c). Iron complex receptor proteins are closely associated with iron transporters, which serve as vectors for the microbial acquisition of iron-containing oxides and hydroxides (Zhou et al. ). These results suggested that AC could generate more iron oxides by promoting iron electron transfer, thus accelerating the uptake and utilization of iron complexes by microorganisms. Previous studies have confirmed that the uptake of iron by bacteria could promote the activity of nitrate and nitrite reductase (Pintathong et al. ; Zou et al. ). Thus, the presence of AC could assist in the enhancement of the inherent denitrification capacity of related bacteria strains by mZVI.
Nitrate reductase of anaerobic denitrifying bacteria is normally integrated with the cell membrane, and NADH dehydrogenase employs a redox medium as the electron shuttle under anaerobic conditions (Sarkar et al. ). The redox medium in this study was primarily the substrate used by denitrification microorganisms, such as scattered ferric ions and their compounds in solution. Besides, genes encoding for NAD(P)H dehydrogenase (K), ubiquinone (K) and riboflavin (K, K) biosynthesis were identified with higher relative abundance in reactor 2-MPDR (Additional file 1: Fig. S6), and these substances combined to promote the electron transfer process reagarding NO3&#; reduction. Based on the above results, the nitrogen metabolism and electron transfer pathways during denitrification were configured and displayed (Fig. 5). Overall, CMC increased the relative abundance of denitrification functional genes in 2-MPDR, demonstrating the enhanced bio-denitrification capacity in denitrification reactors, while AC further accelerated the electron transfer and nitrogen metabolism processes by promoting iron oxidation and hydrogen production.
Fig. 5Involvement of relevant enzymes in the conversion of nitrogen species and the process of electron transfer. CoQ coenzyme Q, SDH succinate dehydrogenase, Cyt c cytochrome c, UQH2 panthenol
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3.5
Acidification enhanced the electron transfer capacity of AC in CMC-based multipathway denitrificationAlthough it is known that AC promoted the NO3&#;-N removal performance in 2-MPDR through the denitrification process and increased the expression of enzymes related to nitrogen metabolism, the potential impact of the acidification process on AC has not been confirmed. Results of electrochemical tests performed on AC indicate that the acidification process appeared to confer a higher electron transfer capacity to AC. Four different electrodes were fabricated with virgin carbon (C), HNO3 acidified carbon (C-N), H2O2 acidified carbon (C-H), and HNO3-H2O2 mixed acidified carbon (AC). As shown in Fig. 6a, the peak current varied between electrodes with different carbons applied. It was observed that AC exhibited the highest current of 1.78 mA, while the others exhibited currents of 1.32 mA (C-N), 0.79 mA (C-H) and 0.35 mA (C) around 0.6 V, respectively. The enhancement of peak current indicated a significant elevation of electron transfer capacity at the electrodes using AC. Theoretically, the area of the enclosed area represents the number of electrons transferred from the electrode and consequently reflects the capacitance of the electrode (Cakici et al. ; Zhong et al. ). The largest closed area was reached in the CV curve of AC, indicating that the mixed HNO3-H2O2acidification process assigned greater electrochemical activity and capacitance to AC compared to other carbon-based electrodes (Wu et al. ). Consequently, AC with a faster electron transfer rate can facilitate the electron transfer in the oxidation of Fe0 and NO3&#; reduction process in denitrification reactors.
Fig. 6The electrochemical properties of carbon with different acid treatments were tested using a three-electrode system of carbon. EIS curves a and CV curves b of C, C-H, C-N, AC, c O1s XPS survey spectra of AC and C
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As an indication of electrode potential loss, EIS analysis was performed to determine the Nyquist curves for the different carbon electrodes. The ohmic resistance obtained from the Nyquist curve is the electron transfer barrier induced by the electrical circuit structure and electrodes. Smaller diameter of the circle in the low-frequency region represents smaller resistance. Our results showed that AC demonstrated the smallest impedance arc diameter, followed by C-N, C-H and C (Fig. 6b). The unique half-circle in the high-frequency region illustrated the absence of diffusion effects in the circuit. Thus, AC could obtain higher currents, larger capacitance and lower apparent resistance, which indicated the expected potential to increase the electron transfer rate.
Further, XPS analysis on the carbon surface was performed to ascertain the mechanism of the enhanced electron transfer rate of AC. The results showed that the acidification process significantly increased the relative oxygen content of the carbon surface (Fig. 6c). The relative area of the O1s peak containing OH&#; and H2O increased by 77.4% after acid modification. Among them, the peak corresponding to OH&#; showed a significant increase in area, while the peak corresponding to lattice oxygen (H2O) remained unchanged (Goh et al. ). The addition of numerous oxygen-containing functional groups (hydroxyl and carboxyl groups) to the surface of carbon during acid modification process endowed it with unique redox properties, which could be responsible for the enhanced electron transfer rate. As previously mentioned, AC with higher capacitance and electron transfer rates exhibited considerable potential in promoting nitrogen metabolism by indirectly enhancing hydrogen production and iron oxidation.
3.6
Potential for advanced nitrate removal with 2-MPDRTo date, chemical and mixotrophic denitrification using the iron-carbon micro-electrolysis system is an effective solution for NO3&#;-N removal in secondary effluent and wastewater. Thus, carbon plays an important role in facilitating electron transfer and improving the microstructure. However, the iron-carbon micro electrolysis system still faces challenges. The low loading of Fe0 on carbon, susceptible oxidation, and paucity in nitrogen selectivity of conventional iron-carbon composites seemed to block further practical application. Limited contact area, poor electron transfer efficiency, and excessive iron usage also restrict the widespread application of simple iron-carbon compounds. CMC in this study could effectively help to improve the mentioned downsides and reduce iron consumption while ensuring an advanced NO3&#; removal rate through the denitrification process. Through the removal effect of trichloroethylene to the iron oxide layer on the CMC surface, the original denitrification performance of CMC can be regained after regeneration (Ritter et al. ). In addition, the lower manufacturing cost of CMC and the operating budget of 2-MPDR alleviate the concerns of practical applications. Combined with the contribution ratios of chemical, autotrophic and heterotrophic denitrification pathways mentioned above in this study and the equation concerning heterotrophic denitrification (Additional file 1: Text S5) (Mccarty ), the amount of additional carbon source required for complete denitrification was calculated. With an average influent concentration of 40 mg L&#;1 NO3&#;-N in 2-MPDR, an additional 7.82 mg L&#;1 methanol was required by calculation. This calculation was performed under the influent containing NO3&#;-N only, while the actual methanol demand will become greater in response to the consumption of NO2&#; and NH4+. Therefore, reducing additional carbon sources while maintaining the denitrification performance of CMC in low C/N ratio wastewater is of great practical importance for the efficient utilization of resources. Future research should target the operation mode of 2-MPDR to develop alternative removal strategies for water columns with various C/N ratios and mitigate additional operating costs.
Our Advantages
10,000 square meters of water treatment filler production workshop
20,000 square meters of high-end environmental protection equipment production workshop
square meters large open laboratory
More than 30 productive experimental bases
More than 40 pilot systems
More than 50 small pilot test devices
More than 60 large instruments and equipment
More than 50 petents
More than 18 years of experience
Top 5 position of environmental protection technology industry in Shandong province, China.
Product Description
This series of catalysts is a kind of multi-component catalytic oxidation catalyst developed for the characteristics of organic wastewater which is difficult to degrade and biochemical. It has obtained a national invention patent and is the inventor of a new micro-electrolytic catalyst in China. It is a new type of unbonded micro-electrolytic catalyst, which is produced by multi-metal alloy fusion catalyst and high temperature microporous activation technology. When acting in wastewater, COD can be removed efficiently, chroma can be reduced, biodegradability can be improved, the treatment effect is stable and lasting, and the phenomenon of catalyst passivation and hardening can be avoided in the process of operation.
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Product Parameters
Catalyst Parameters
Model
Specific Gravity (T/m³)
Poriness
Prsessure (kgf/cm²)
Granul Size (cm)
Catalytic
LEMBR-01
1.3~1.6
&#;65%
&#;600
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1~3, 3~5, 5~10
Noble Metal
LEMBR-02
1.3~1.6
&#;65%
&#;600
1~3, 3~5, 5~10
Rare-earth Metal
LEMBR-03
1.3~1.6
&#;65%
&#;600
1~3, 3~5, 5~10
Composite Metal
Technological Advantage
(1) The alloy structure ensures that the "primary battery" continues to be highly efficient.
(2) Bigger specific surface area improves current density and better catalytic oxidation effect.
(3) High activity, low density, no passivation, no hardening, fast reaction rate, long-term stable and effective degradation resuits.
(4) Improved oxidation efficiency and expanded application range for wastewater treatment.
(5) Greatly reduces the operating intensity of workers.
(6) The treatment of wastewater by the filler integrates the oxidation, reduction, electro-deposition, flocculation, adsorption, bridging, sweeping and co-precipitation processes.
(7) The treatment cost is low and the wastewater biodegradability is greatly improved.
(8) The supporting facilities can be customized.
Application Field
1. Dye, chemical, pharmaceutical wastewater; Coking and petroleum wastewater;
-- COD value decreased significantly and BOD/COD value increased significantly after the wastewater treatment.
2. Printing and dyeing wastewater; Leather wastewater;
-- Good application for decolorization and obvious removal of COD.
3. Electroplating wastewater; Printing wastewater; Mining wastewater; Other wastewater containing heavy metals;
-- Heavy metals can be removed from the above-mentioned wastewater.
4. Organic phosphorus agricultural wastewater; Organochlorine agricultural wastewater;
-- Greatly improve the biodegradability of the above wastewater, and can remove phosphorus, sulfide.
Related Products
MICROELECTROLYSIS CATALYTIC OXIDATION REACTOR
This reactor mainly be used in micro-electrcolysis technology for wastewater treatment. The micro-electrolysis technology is an ideal process for high-concentration refractory organic wastewater treatment. This process is mainly used for high-salt, refractory and high-chroma wastewater treatment. The technology can not only reduce COD and color with low cost, but also greatly improve the biodegradability of wastewater. The process has the advantages of wide application range, good treatment results, low cost, short treatment time, convenient operation and maintenance, as well as low power consumption etc. The technology can be widely applied to pretreatment and advanced treatment of various industrial wastewater.
Certifications
National high-tech enterprises
The "little giant" of specialized and sophisticated enterprises national
Specialized and sophisticated enterprises that produce new and unique products of Shandong province
Shandong gazelle enterprise
Shandong province research and development center
Shandong Industrial Design Center
Hidden champions
ISO quality system certification enterprise
ISO Occupational health and safety management system certification enterprise
ISO environmental management system certification enterprise
More than 50 invention patents and 10 utility model patents granted
Company Profile
Shandong Longantai Environmental Protection Sci-tech Co., Ltd. was founded in , integrated R&D, manufacturing, process design, project construction and water treatment, focusing on the efficient treatment and comprehensive utilization of industrial wastewater and high-salt wastewater, and providing energy-saving, efficient, resource recycling solutions and key materials and equipments.
Longantai has accumulated rich experience in the pretreatment of high-concentration industrial wastewater, advanced wastewater treatment, comprehensive treatment of high-salt wastewater, water reuse in wastewater, wastewater recycling and other aspects. There are strong strength and perfect quality system in the research and development and manufacturing of water treatment catalysts and key equipments.
CASE INFERENCE
1. Chemical/pharmaceutical/industrial park comprehensive wastewater pretreatment and upgrading
2. Coal chemical wastewater treatment
3. Petrochemical energy wastewater treatment
4. Dye/pigment wastewater treatment
5. River water quality improvement
6. Pesticide wastewater treatment
7. Reverse osmosis membrane concentrated water treatment
8. Leather waste water treatment
9. Total treatment technology of landfill leachate
10. Electroplating wastewater treatment
FAQ
1.Q: Where is your company? How can I visit there?
A:The company is located in Zhongcheng International, Kuiwen District, Weifang City, Shandong Province, China. It is about an hour's drive from Qingdao Airport and Weifang Railway Station. If you need it, we can come and pick you up. Welcome to visit our company.
2.Q:Do you have minimum order quantity request?
A:No minimum order, but it can get a discount if you order a large quantity.
3.Q:Do you have certificates?
A:Yes,we have ISO,SGS certificate.
4.Q:Can you meet my special requirements for the product?
A:Yes,we have a professional design team.We can provide drawings according to your requirements.
5.Q:How to buy your idea products?
A:You can provide us your water or waste sources,water or waste quality,flow rate and ground area (connect us for more details)
6.Q:How to pay?
A:T/T and L/C are acceptable and T/T will be more appreciated 30% deposit before producing,70% balance before loading by T/T.
7.Q:What is the delivery time ?
A: It depends on order quantities .Generally speaking ,the delivery time will be within 2 to 4 weeks.
8.Q:How to pack the products?
A:We use standard package .If you have special package requirements ,we will pack as required ,but the fees will be paid by customers.
9.Q:How to install after the equipment arriving destination?
A:We will provide detailed illustrations to you. If it is necessary, we will send technicians to help you. However, the visa fee ,air tickets ,accommodation, wages will be paid by buyers.
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