The POPs (Persistent Organic Pollutants) are frequently detected in treated sewage, surface, groundwater, and even drinking water, and have been observed to be capable of long-range transport, Bioaccumulate in human and animal tissue, Biomagnify in food chains, and to have potentially significant impacts on human health and the environment . The discharge of wastewater containing dye effluents is a significant source of pollution in the ecosystem. These effluents are proven to be carcinogenic agents, in terms of esthetic and prevailing aquatic flora and fauna . The wide discharge range of synthetic dyes produced and being increasingly used by different industries in ecosystems made this subject a major environmental problem . Dyes are basic daily chemical compounds and are widely used in many fields to color their products such as textile, leather, paper, rubber, printing, plastics, etc . About 200 L of water is needed to produce 1kg of textile and about 1.6 million L of water is consumed for an average-sized textile mill per day . Dyes molecules in wastewater lead to mutagenicity, carcinogenicity, and dysfunction of human beings’ kidneys, liver, brain, reproductive system, and central nervous system . Azo dyes are not biodegradable and their
presence in water, in addition to adverse esthetic effects, reduces light penetration into water and interferes with aquatic life. Additionally, they are toxic, carcinogenic, and mutagenic to humans . The coloring system of azo dyes includes a group (-N=N-) with one or more aromatic groups . Azo dyes widely use in the textile, ink, paper, plastics, food, and cosmetics industries  and Compounds containing azo dye are toxic, carcinogenic, and mutagenic for aquatic organisms [4, 10, 12]. They are also highly stable in the environment and pose a threat to human, animal, and plant species if they enter the environment . The development of advanced water treatment technologies with low-cost and high efficiency to treat the POPs contaminated wastewater is desirable . Currently, available water treatment technologies such as adsorption or coagulation merely concentrate the pollutants present by transferring them to other phases, but they are not completely “eliminated” or “destroyed” . Other conventional water treatment methods such as sedimentation, filtration, chemical oxidation, and biotechnology suffer from some disadvantages such as incomplete removal, high consumption of chemical reagents, high treatment cost, time-consuming, and generation of toxic secondary pollutants . Biological and enzymatic treatment and detoxification, Membrane technologies, photolysis, and electrochemical coagulation for the degradation of hazardous dyes are the new dye removal processes. The photodegradation process of POPs has attracted increasing attention during the past decades due to its effectiveness in rapidly degrading and mineralizing recalcitrant organic compounds and its very high efficiency as well as the absence of secondary contaminants and is used to remove various types of contaminants such as dyes [8,17,18, 19]. The advantages of heterogeneous photocatalytic techniques that make them superior to traditional methods include the removal of pollutants in the range of ppb, production avoidance of polycyclic compounds, and the costVarious photocatalysts including CdS, SnO2, WO3, SiO2, ZnO, Nb2O3, and Fe2O3 were being studied but the nano-TiO2photocatalyst is well-known among the metal oxides for its high efficiency, low cost, physical and chemical stability, widespread availability, and noncorrosive property . TiO2 nanomaterials mediated advanced wastewater treatment technique has considerable potential for the removal of various types of complex organic pollutants from wastewater under visible, solar, and UV light sources [20, 23, 24]. Titanium dioxide is technically an important compound that has been widely considered. This compound has useful features, such as low cost, commercial accessibility, chemical stability, biocompatibility, and nontoxicity . In general, AOPs are processes in which by various methods, including a strong oxidizing agent such as hydrogen peroxide, ozone and a catalyst such as zinc oxide, titanium dioxide, and iron, in the presence or absence of ultraviolet radiation, that produces active hydroxyl radicals [29,30,33]. The rationales of AOPs are based on the in situ generation of highly reactive transitory species (i.e. H2O2, OH●, O2-, O3) for the mineralization of refractory organic compounds, water pathogens, and disinfection by-products [26, 27]. Due to their high oxidation capacity of 2.8v, hydroxyl radicals can convert organic chemical pollutants to minerals and have a high efficiency in the oxidation of resistant organic compounds . Due to the possibility of converting raw materials into intermediate compounds with more toxicity in these processes, bioassay studies using different species of living organisms such as fish, algae, bacteria, animal cells, zooplankton, and freshwater organisms done like Daphnia Magna . Due to short reproduction, high sensitivity, ease of use, low laboratory costs, and most importantly, the ability to reproduce and produce offspring of a genus with genetic similarity, to monitor the effluent and determine the efficiency of treatment plants to Reduction of toxicity has been high, Daphnia Magnaregarded by researchers . In a study using Daphnia magna and Vibrio fisheri, experiments indicated that among these organisms, Daphnia magna is more sensitive to environmental pollutants . In this study, decolorization and detoxification of dye solution containing D.Y 50 dye and real textile effluent by nano photocatalytic process were investigated using Daphnia Magna. The effect of factors such as TiO2 dosage and initial dye concentration, irradiation time, pH, and interfering factors in the environment on the efficiency of the decolorization process was investigated and after optimizing these factors, using the bioassay method by Daphnia Magna Toxicity reduction was studied.
materials and methods
The textile azo dye, C.I. Direct Yellow50 (D.Y50), was procured from AlvanSabet, Hamedan Company. The molecule structure and structural information of the dye are shown in Table 1. The TiO2 nanoparticles were procured from Nano Green Company, Tehran. The physical and chemical properties of TiO2 nanoparticles are shown in Table 2. Other chemicals used in this study were obtained from Merck Germany with a purity of >99% and deionized laboratory water was used for making aqueous mixtures.
Design and construction of a reactor
The photocatalytic degradation was carried out in a 2 L cylindrical Plexiglass reactor with 7 UVA (PL, HHZM. Co. 9W, low-pressure Hg lamp close to bottom) The UV light sources were surrounded by a Quartz glass tube to prevent direct contact with the solution and the reactor schematic is shown in figure1. The intensity of the lamps was measured by a radiometer EC1 UVA by Silicon photodiode detector, It was UVA = 5.4 (mw / cm²). The wavelength range was UVA (315-400).
Preparation of D.Y50 dye calibration curve
To determine the λ-max of the D.Y 50 dye sample, the dye sample was scanned by Shimadzu/UV Probe2700i. It is a double monochromator system capable of 8-Abs measurements. This probe uses the integrating sphere, for the analysis of samples in the wavelength range of 300nm to 1400nm.The D.Y 50 dye λ-max obtained 402 nm. The dye stock solution (1000 mg/l) was prepared and then standard concentrations of 0.25 to 500 mg/l stock solution were prepared to draw the absorption calibration curve of the dye.
The photocatalytic experiments were conducted to investigate the degradation of the D.Y 50 dye in aqueous suspension. The dye removal by TiO2 in a reactor containing a UVA lamp was performed by following steps: 4 ranges 2, 5, 7, and 9 of pH were used to evaluate the effect of pH on the reactions. Initially, pH was obtained by using constant concentrations of 80 mg/l dye and 2 g/l TiO2. The next step, was applying the optimal pH, various initial dye concentrations 20, 40, 60, and 80 mg/l, and various TiO2 concentrations 0.1, 0.25, 0.5, 1, 1.5, and 2 g/l respectively. Sampling was conducted from the reactor at intervals of 5, 10, 15, 30, 60, 90, and 120 minutes. The effect of pH, catalyst dosage, initial dye concentration, contact time, and the presence of interfering materials on the efficiency of the studied processes was investigated. The experiments were triplicated. Control samples were considered to investigate the effect of each catalyst and UVA light alone on the dye decomposition process. To investigate the effect of interfering agents, the experiments were repeated under optimal conditions with real dyeing wastewater, and the reaction rate constant was compared to synthetic conditions. To determine the characteristics of real wastewater, the COD test was performed by reverse distillation method. A sample is refluxed in a strongly acid solution with a known excess of potassium dichromate. After digestion, the remaining unreduced dichromate was titrated by ferrous ammonium sulfate to determine the amount of potassium dichromate consumed and the oxidizable matter calculated in terms of oxygen equivalent. The BOD method consists of filling with samples. To overflow, an airtight bottle of the specified size and incubate at the specified temperature for 5 days. Dissolved oxygen was measured initially and after incubation, and the BOD was computed from the difference between the initial and final DO (40). The pH was adjusted to the required value by 1N H2SO4 or 1N NaOH. The pH is measured by a German Cyber scan pH meter. An injection pump (AEG– MS633-4 – Germany, 60 Lit/h, 220v) was used to mix and prepare a homogeneous solution during the experiment. After UV light irradiation for a certain time interval, each sample was centrifuged to separate the suspensions of the TiO2 nanoparticles by the Hettich Universal x1000U/min at 4000 rpm at ambient temperature for 10 minutes and the residual dye concentration was determined by a Genesys 8 Type Spectrophotometer during the maximum wavelength was measured at 402 nm. The Genesys 8 Type Spectrophotometerinclude an automatic 7-position sample holder as standard and Wavelength Range is about 200 to 1100 nm.To determine the reaction kinetics, zero, one, and two models are used, and the model that shows the highest R² was determined as the reaction model, and its kinetic parameters were reported.
To determine this parameter, 0.1 M NaCl was used as an electrolyte, and 0.1 M caustic soda and hydrochloric acid solutions were used as pH control. Poured 35 ml of the electrolyte solution into six Erlenmeyer 50 ml and the pH of solutions adjusted in the range of 2 to 12 using acid and caustic soda. 0.2 g of catalyst nanoparticles were added to each Erlenmeyer. To control the results, an Erlenmeyer containing electrolyte without nanoparticles was considered as a control. The contents of each Erlenmeyer were centrifuged (3000 rpm for 15 minutes) and after the above time elapsed, the final pH was read. The pHzpc point was determined by plotting the initial pH values against the final values. [22, 41].
The first generation of the daphnia used has preyed from its natural habitat. The culture medium used for Daphnia culture was based on the standard method, which includes ordinary municipal dechlorinated water with nutrients 0.192 g/l sodium bicarbonate, 12 g/l calcium sulfate, 0.008 g/l potassium chloride, and yeast. The culture medium was aerated using an aquarium pump for 6 hours a day. In the first step, one of the preyed D. magna was cultivated according to the above-mentioned instructions. D. magna were then nourished to reach their reproductively active life cycle. At 20°C D. magna reach sexual maturity in 6–8 d releasing their eggs into a brood chamber. The embryos complete their development inside the brood chamber and hatch as free-swimming neonates on days 8–10. In the following 2–4 d the mature females release a second brood of neonates with reproduction peaking around the third brood (day 12–14) or fourth brood (day 14–17). As the adult daphnids become older the time between broods will increase and the size of the brood will decrease [33,42]. This generation has the same mother that was used for herd cultivation. Therefore, all of the D. magna used in the present study were genetically quite the same. To test for toxicity in each series, 4 containers with concentrations of 0, 5, 10, and 20 mg/l of dye were prepared and in each concentration, 10 Daphnia with the same genetic traits were used. The colorless sample was used as a control sample. All experiments are triplicated. The tests were performed according to standard procedures and EPA-821-R-02-012 directives. Data analysis and calculation of LD50 were performed using Probit statistical method with SPSS 16.0.
pH is considered an important factor since it influences the surface charge properties of the catalyst. To study the effect of initial pH on the degradation of D.Y 50 dye, experiments were conducted by varying the pH in the range of 2–9. The amount of active hydroxyl radical produced by UV rays and the amount of effective dye removal depends to a large extent on the pH values of the reaction solution . The pHzpcof TiO2was 6. The experimental conditions were an initial dye concentration of 80 mg/l, a TiO2 concentration of 2 g/L, and an irradiation time of 120 min. Figure 2 shows the effect of pH on the D.Y 50 dye degradation. The degradation after 120 min irradiation was (lnC0/C= 1.4)at pH 2. In the UVA/TiO2 process at pH 2, the dye concentration half-life and the reaction rate constant had the lowest and highest values was214 min and 0.1542 min-1 respectively.
Effect of Initial Dye Concentration
The effect of initial dye concentration on the removal rate was investigated at the optimum pH of 2 before being determined. The results showed that in UVA/TiO2 process, by increasing the initial dye concentration and contact time, the dye removal decreased. The highest (lnC0/C = 3) and lowest (lnC0/C = 0.6) dye removal efficiency in UVA/TiO2 photocatalytic process by 1g/l TiO2 concentration, occurred in 20 mg/l and 80 mg/l initial dye concentration respectively. Figure 3 shows the effect of initial dye concentration in the UVA/TiO2 photocatalytic reactor. As shown in figure3, the dye removal efficiency decreased by increasing the initial dye concentration, these results indicate when the dye concentration increased from 20 to 80 mg/l, the dye removal efficiency decreased respectively. The results revealed a gradual decrease in photodegradation activities with increasing the concentration of D.Y 50 dye. Low concentration of D.Y 50 dye (20 mg/L) has high removal efficiency reaching lnC0/C = 3. This is due to the presence of a sufficient surface area of the provided catalyst and low intermediate production at a low D.Y 50 dye concentration. However, the rich formation of intermediate products at high concentrations of D.Y 50 dye at constant photocatalyst dose would be competing with the D.Y 50 dye molecules themselves onto the photocatalytic surface, which might explain the decreased degradation of D.Y 50 dye. To control the above steps under optimal pH conditions, the initial dye concentration of 20 mg/l and 1g/l TiO2 catalyst without UVA radiation (dark condition) was taken as a control sample. The results showed the dye removal percentage in These conditions was very insignificant (0.54%). Also, as a control sample, the dye removal in 20 mg/l initial dye concentration and UVA radiation (without catalyst) was measured, and the dye removal percentage in these conditions was very low (0.06%). According to the first-order kinetic equation, the highest reaction rate constant of the UVA/TiO2 process was K= 0.4342 min-1, which indicates the highest reaction rate at the mentioned concentration of titanium dioxide and initial dye concentration compared to other concentrations. Also, according to these equations, the D.Y 50 dye half-life (t1/2) was the lowest in the initial concentration of 20 mg/l.As expected there is a reverse relationship between the photocatalytic degradation of D.Y 50 dye and its initial concentration. It is when the initial dye concentration was increased, more dye molecules adsorbed on the surface of TiO2. The existence of large amounts of adsorbed dye results in the lack of any direct contact with the holes or hydroxyl radicals. This might have an inhibitive effect on dye degradation. Another possible reason for these results is the effect of UV screening of the dye. At high dye concentration, the solution with a higher concentration may absorb more fraction of the emitted UV radiation than a lower initial dye concentration, and as a result, the number of available photons may decrease, leading to a reduction in the formation of OH● radicals. On the other hand, the hydroxyl radical concentrations remain constant for all dye concentrations while the dye molecule increases as the initial concentration of dye increases, hence the degradation efficiency decreases . Another possible reason is the formation of intermediates during the dye molecules' degradation. [59,61].
Effect of Catalyst Dosage
The effect of TiO2 dosage on the D.Y 50 dye removal was studied and the results of the UVA/TiO2 process are shown in figure4. The experiments were carried out at 20 mg/l dye concentration for 120 min. The removal efficiency increases by increasing the catalyst dosage and then become constant in a specific catalyst dosage. The most effective decomposition of D.Y 50 dye was observed at 1 g/l of TiO2 dosage. The enhancement of photocatalytic efficiency as a result of increasing photocatalyst dose could be explained based on increasing the available surface area of the photocatalyst and the formation of more active radicals and thought this observation is thought to be that all dye molecules are adsorbed on TiO2.In addition, the present results showed a relative decrease in photocatalytic efficiency that was observed at dose 2 g/L Compared with 1.5 g/L due to the lack of light penetration and the photocatalytic cumulative effect in the solution .The addition of higher quantities of TiO2 would not affect the degradation efficiency. The cause of this is supposedly an increased opacity of the suspension, brought about as a result of excess TiO2 particles [50,57]. Figure 4 shows the highest decolorization rate (lnC0/C= 2.9) in the presence of 20 mg/l D.Y 50 dye initial concentration and 1g/l TiO2 catalyst. When the TiO2 dosage increases more than 1g/l, the catalyst particles may agglomerate and this results decreasing in removal percentage .
Impact of interfering factors
The COD concentration in real wastewater was 610 mg/l. In the synthetic process 20 mg/l initial dye concentration and 1 g/l catalyst dosage, 50, 100, and 150 mg/l of COD were prepared. As shown in Figure 6 the highest dye removal (85%) at 50 mg/l COD concentration occurred. Dye removal efficiencies at 100 and 150 mg/l COD concentrations were 75% and 70%, respectively. As shown in Table 3, the reaction rate constant in real wastewater under optimal conditions of the UVA/TiO2 process was in the range of 0.28 and 0.12 While the reaction rate range in the synthetic sample was between 0.36 and 0.14.
Comparing figure 7 and 8 which shows the Daphnia Magna death percent by contact with different D.Y 50 dye effluent concentration before and after UVA/TiO2 process, indicate the high toxicity of D.Y 50 dye before degradation. In this way, the D.Magna death percent when exposed to 20 mg/l initial dye concentration before detoxification at the maximum contact time (96 h) was % 97, while this rate after degradation by UVA/TiO2 process by the same initial dye concentration and contact time, decreased to % 41
The pH influences the characteristics of the photocatalyst surface charge, hence pH of the solution is a significant parameter in performing the reaction on the surface of TiO2 for the photocatalytic degradation of dyes . According to the results, the dye removal rate increased by decreasing pH. The cause of this phenomenon is due to the anionic D.Y 50 dye structure and the TiO2 catalyst pHzpc which is 6. Accordingly, due to the positive charge of TiO2 surface at pH below 6, aspH decreased, and the number of positive charges and the electrostatic attraction between catalyst and pollutants and dye removal efficiency increased respectively [44,48]. When pH increases, the number of negatively charged sites increases, and since negative sites on the photocatalyst surface cannot be effective in adsorbing colored anions, increasing the pH will reduce the photocatalyst's ability to degrade and decolorize . In addition, from the previous studies, the change in pH around the ZPC point, causes the stick together of catalyst particles, resulting in particle deposition, which will reduce the removal efficiency [31,38].S. K. Patel et al. 2020, Investigated the photocatalytic degradation of reactive dye in aqueous solution by Fenton, Photo-Fenton andTiO2. They observed that at a solution with pH of 3 and 4 and lower, dye removal efficiency was greater at UV–TiO2process. Mirzadeh et al At higher pH values, the dye removal efficiency decreased exponentially. The results of this study showed that most dye removal occurs in the acidic pH range, and the results are in agreement with the present study . A study conducted by Kaur et al demonstrated that as the pH decreased, dye-ionized molecules are adsorbed on the surface of the TiO2 catalyst . Mai et aland Shafaei et al, found that at pH less than 9, active levels of positively charged zinc oxide catalysts were coated by dye molecules. Therefore, the production of hydroxyl ions and consequently hydroxyl radicals is reduced. On the other hand, at pH above 9 due to the presence of hydroxyl ions, the surface of the catalyst has a negative charge and the dye adsorption decreases due to its structure at the catalyst level [34,38]. These studies confirm the results of the present study.
Effect of initial dye concentration
Initial dye concentration is one of the most important parameters at the photocatalytic dye decomposition rate which has a significant effect on decomposition efficiency. The photocatalysis depends on the adsorption of dyes on the surface of the photocatalyst. In the photocatalysis process, only the amount of dye adsorbed on the surface of the photocatalyst contributes and not the one in the bulk of the solution . Dye removal decreased with increasing initial dye concentration indicating that as the dye concentration increases, more dye substances are adsorbed on the surface of TiO2, whereas fewer photons are available to reach the catalyst surface and therefore less ∙OH radicals are formed, thus causing an inhibition in degradation percentage. Also according to Beer-Lambert law, as initial dye concentration increase, the amount of light or photons passing into the solution decrease, and when trapped and absorbed on the dye particle surface, it causes reducing the absorption of photons on the catalyst and production of radicals respectively. Eventually, it reduces the decomposition rates [37,44,71]. A study conducted by Ghanbarianet al, mentioned that a reason for the decrease in reactive orange dye removal efficiency was the UV-Screening of dye. At high dye concentrations, a large amount of UV radiation may be absorbed by dye molecules instead of being absorbed by TiO2 particles, which reduces the efficiency of the catalytic reaction by reducing the concentration of hydroxyl and O2 radicals . Kumar et al. 2017, concluded that the initial methyl orange dye concentration reduction in the effluent caused turbidity reduction, and increasing its concentration caused adsorption on the catalyst surface, followed by a decrease in the active surface . Previous studies have also reported the dependence of the UV-TiO2 catalytic reaction rate on the initial concentration of contaminants. According to these studies, increasing the initial concentration of dye in this process causes saturation of the catalyst surface, thus reducing the UV absorbance on the catalyst surface and reducing the photocatalytic decomposition rate [17, 45]. The results of Chakrabarti and Mai's study confirm that at dye degradation by UV/ZnO photocatalytic process, as initial dye concentration increased, the dye removal rate decreased. A reason for this reduction is the adsorption of contaminants on the catalyst surface and consequently declining of active sites on the catalyst surface [44, 51]. Mahvi et al. 2016showed that by increasing the initial Direct Red 23 azo dye concentration from 25 to 200mg/L, dye removal efficiency decreased from 99.2 to 20% . According to obtained kinetic equations, the reaction rate constant for the UVA/TiO2 process at a concentration of 1 g/l titanium dioxide and initial dye concentration of 20 mg/l was K = 0.4344, which indicates a higher reaction rate than other concentrations of catalysts and dyes are present in this reaction. Also, according to this equation, the D.Y 50 dye half-life (t1/2) for the UVA/TiO2 process with the above conditions was 23 min.
Effect of Catalyst Dose
As mentioned and shown in figure5, increasing the catalyst concentration increases the active levels of the catalyst and consequently, this process increases the hydroxyl production and other oxidizing radicals [43, 84]. Although this increase in catalyst concentration has a positive effect on the photochemical decomposition process but reduces the decomposition rate by increasing the catalyst concentration to higher than the optimum concentration due to the increase in turbidity, causing light scattering and decreasing the UV penetration . Chakrabarti et al. 2004, showed that by increasing ZnO catalyst concentration, the photocatalytic decomposition rate increases due to an increase in active surfaces on the catalyst and consequently the increase in the production of hydroxyl radicals. Increasing the catalyst concentration higher than the optimal range reduces the decomposition rate. The main reason is the increase in turbidity and interference with the light passage into the solution . Barakat et al. 2010, indicated that increasing TiO2 dosage to the optimum dose increased the dye decomposition rate. The reason is the increase in dye adsorption on the catalyst surface due to an increase in its concentration . According to Mahvi et al. 2015 as the dose of the nanoparticle increases from 0.2 to 1 g/L dye removal of RB 19 increases, when other parameters are kept constant. With increasing nanoparticles dose more adsorption sites are for the adsorption of RB 19 and consequently, dye removal raises .
Impact of interfering factors
The presence of interfering factors in the actual wastewater reduces the reaction rate due to the consumption of hydroxyl produced in the process. Sobczynski et al. 2001 found that a High concentration of pollutants in water saturates the TiO2 surface and hence reduces the photonic efficiency and deactivation of the photocatalyst. Daneshvar et al. 2007, show increasing organic compounds by increasing the turbidity in the solution, prevents the penetration of light and reduces the absorption of UV photons on the catalyst surface, and ultimately, reduces the dye decomposition rate . The above result confirms the results of the present study.
Catalytic process in the presence and absence of UV rays
The low decomposition percentage of D.Y 50 dye in the control sample (0.49%) is due to the major role of UV radiation in the production of highly active hydroxyl radicals . By UV radiation alone, the dye removal efficiency was very low (0.04%). This indicates that hydroxyl radical production which requires the presence of the catalyst, has a major role in the dye decomposition initiation. Also, there was proved that the presence of the catalyst and UV radiation together is the vital factor for initiating and accelerating the photochemical reaction .
Most of the aromatic dyes and other aromatic pollutants could be toxic to various organisms, specifically aquatic organisms and plants [62,63]. One of the photocatalytic degradation processes aims is the decreasing or elimination of toxicity associated with the compounds being treated. The toxicity test results on D. magna showed that obtained lethal concentration of 50% (LC50) from 24 to 96 hours contact time of D.Y 50 dye effluent before degradation varies from 66 to 16 mg/l. According to EPA guidelines, the D.Y 50 dye is in the relatively toxic group (LC50 greater than 100 in the relatively non-toxic group, 10-100 in the relatively toxic group, 1-10 highly toxic, and less than 1 is ultimately toxic). According to the obtained results, the Toxicity Unit index (TU) of the dye varies from 1.52 to 6.25. As results show in Table 4, based on the EPA guideline, the effluent after UVA/TiO2 photocatalytic process is in a relatively non-toxic group (24-hour LC50 equal to 115 mg/l). Goyal et al. 2010, were used D. magna, Vibrio fisher, and microalgae to evaluate the degree of toxicity reduction in photocatalytic degradation processes. Results showed among these organisms, D. magna and Vibrio fischer were more sensitive to pollutants respectively . Mahvi et al. 2007 and 2011 in studies conducted on the RO16 and AO7 dye toxicity reduction, concluded that UV/TiO2 photocatalytic process and horseradish peroxidase (HRP) have a favorable effect on the removal and reduction of the dye toxicity [53, 79]. All results of the previous studies confirm the present study's findings.
Bioassay test and Biodegradability Index (BOD5/COD rate) Comparison to confirm UVA/TiO2 process detoxification efficacy
To confirm the photocatalytic degradation efficacy on detoxification of D.Y 50 dye effluent, bioassay test and biodegradability index (BOD5/COD rate) were compared. The levels of biochemical oxygen demand (BOD5) and chemical oxygen demand (COD) of wastewater could pose potential pollution to water bodies in which they are discharged Typical values for the ratio of BOD5/COD for untreated municipal wastewater are in the approximate range of 0.3 to 0.8 as shown in Table5[65, 66, 67]. If BOD5/COD is > 0.6 then the waste is fairly biodegradable and can be effectively treated biologically. If BOD5/COD ratio is between 0.3 and 0.6, then seeding is required to treat it biologically, because the process will be relatively slow, as the acclimatization of the microorganisms that help in the degradation process takes time. If BOD5/COD is <0.3, biodegradation will not proceed, thus it cannot be treated biologically, because the wastewater generated from these activities inhibits the metabolic activity of bacterial seeds due to their toxicity or refractory properties . It is called the Biodegradability Index (B.I.). It is generally considered the cut-off point between biodegradable and non-biodegradable waste . According to Figure 9 and comparing the B.I. values of effluent before and after degradation to the mean B.I. can assist in monitoring the presence of toxic and non-biodegradable substances in photocatalytic process effluent. As shown in figure9, B.I. by the maximum exposure time of 120 min, in the control sample without the use of UV and catalyst was 0.25. As mentioned previously, B.I. <0.3 means the presence of toxic or refractory substances in an effluent sample. Therefore, it shows that in the absence of UV and catalyst detoxification of D.Y 50 dye effluent does not happen. On the other hand, it showed that B.I. after D.Y 50 dye effluent degradation at the same condition was 0.68 and it was upper to 0.6 then the effluent was fairly biodegradable. So, the results showed that photocatalytic degradation of D.Y 50 dye effluent by the UVA/TiO2 process enhanced the B.I. of effluent.
By comparing figure9 and 10 and survey changes in bioassay test and B.I. trends, could be interpreted that in photocatalytic degradation of D.Y 50 dye effluent by UVA/TiO2 process over 120 min, B.I. increased from 0.25 to 0.68 and LC50 over 96 h increased from 16 to 44.7 mg/l respectively and respect to figure7 and 8 this means D.magna mortality rate over 96 h decreased from 97.7 to 43.3 respectively. Both of these experiments confirmed UVA/TiO2 photocatalytic degradation process efficacy on detoxification of D.Y 50 dye effluent.
Decolorization and detoxification of dye solution containing C.I.direct Yellow50 effluent by UVA/TiO2 nano photocatalytic process were investigated using Daphnia Magna. The effect of factors such as TiO2 dosage, initial dye concentration, irradiation time, pH, and interfering factors on the efficiency of the decolorization process was investigated and after optimizing these factors, toxicity reduction was studied by bioassay using Daphnia Magna and biodegradability index (BOD5/COD rate). To remove dye by UVA/TiO2 process, 4 ranges of pH 2, 5, 7, and 9, initial dye concentrations 20, 40, 60, and 80 mg/l, TiO2 concentrations 0.1, 0.25, 0.5, 1, 1.5, and 2 g/l, at intervals of 5, 10, 15, 30, 60, 90 and 120 min and daphnia magna were used respectively. As a result, the D.Y 50 dye effluent degradation at pH 2, 20 mg/l initial dye concentration and 1 g/l TiO2 catalyst was (lnC0/C= 1.4), (lnC0/C= 3) and (lnC0/C= 2.9) respectively. dye removal rate by 50 mg/l COD concentration was (88%) and the Daphnia Magna mortality rate after maximum contact time (96 h) decreased from 96.7% to 43.3%. This study also found that by
The authors of this article would like to thank the Vice Chancellor for Research and Technology Development of Kashan University of Medical Sciences for their financial support of this research and for providing the necessary facilities.