CC BY
9
Дослиджено закономiрностi осадження смолистих речовин зi стiчних вод коксохi-мiчних тдприемств при гетерокоагуляцп коагулянтами FeCl3 i А12(ОН)5С1, та бен-тонтовою глиною сумкно з флокулянтом Extraflock Р70. Методом седиментацтно-го аналiзу встановлен швид^сть осадження та переважт ра^уси полютант-вмю-них агрегатiв дисперсног фази стгчних вод. Отриман результати дозволяють удоско-налити процес очищення фенольних вод на коксохiмiчних тдприемствах
Ключовi слова: седиментацшний аналгз, бентонтова глина, стiчнi води коксохiмiч-них тдприемств, смолистi речовини, коагулянт, флокулянт
□-□
Исследованы закономерности осаждения смолистых веществ из сточных вод коксохимических при гетерокоагуляции коагулянтами FeCl3 и А12(ОН)5С1, и бентонитовой глиной совместно с флокулянтом Extraflock Р70. Методом седиментационного анализа установлены скорость осаждения и преимущественные радиусы полютант-содержащих агрегатов дисперсной фазы сточных вод. Полученные результаты позволяют усовершенствовать процесс очистки фенольных вод на коксохимических предприятиях
Ключевые слова: седиментационный анализ, бентонитовая глина, сточные воды коксохимических предприятий, смолистые вещества, коагулянт, флокулянт
UDC 628.312.1: 628.316.13
| DOI: 10.15587/1729-4061.2017.119064 |
SEDIMENTATION OF POLLUTANT-CONTAINING AGGREGATES DURING PURIFICATION OF WASTEWATER FROM COKING PLANTS
D. Yelatontsev
Postgraduate student* E-mail: sauron1 1652@gmail.com V. Suprunchuk
PhD, Associate Professor Department of Inorganic Substances, Water Purification and General Chemical Technology National Technical University of Ukraine «Igor Sikorsky Kyiv Polytechnic Institute» Peremohy ave., 37, Kyiv, Ukraine, 03056 E-mail: OlenaIvanyuk@ukr.net M . V o l o s h i n Doctor of Technical Sciences, Professor, Head of Department* E-mail: voloshin@ua.fm *Department of Chemical Technology of Inorganic Substances Dniprovsk State Technical University Dniprobudivska str., 2, Kamianske, Ukraine, 49000
1. Introduction
The extremely negative impact of coke-chemical enterprises wastewater (due to significant pollution by phenol, called phenolic) is a well-known fact. Numerous scientific papers [1-12] describe it. There are many coke enterprises in Dnipropetrovsk and especially Donetsk regions. A scale of a damaging influence of a mentioned type of man-made waste on the environment is a source of concern for the population of the regions.
Previous studies [1] determined reasons for poor performance of the purification of phenolic wastewater from phenols, rhodanates and cyanides. The main reason is the lack of efficiency of removal of resins at the stage of mechanical purification. Experiments proved the effectiveness of the reagent flotation method with a use of coagulants: Al2(OH)5Cl, Al2(SO4)3, AlCl3, FeSO4, Fe2(SO4)3 and FeCl3 [2]. Treatment with alkaline bentonite clay with the addition of cationic flocculant reduced a content of resins to modern requirements for disposal of sludges in construction of road pavements [3]. This article considers a quantitative description of processes, which occur in the medium of phenolic wastewater during their purification with a use of coagulants, flocculants and bentonite clays.
The literature does not reveal quantitative characteristics of sedimentation of pollutant-containing aggregates of the dispersed phase of phenolic wastewater. Therefore, it is not possible to improve a process of wastewater purification from resins purposefully. Detection of quantitative characteristics of the sedimentation process determines the expedience of the study.
2. Literature review and problem statement
Typical and most common method of purification of phenolic waters from resinous substances is flotation with an addition of special reagents (coagulants or flocculants) [1-3].
Reagent flotation involves the delivery of coagulant solutions to flotators during passing of air through contaminated water. As a result, processes of coagulation, coalescence and oxidation of most organic substances intensify. The best reagents for this purpose are ferrum salts: FeCl3, FeSO4, and others. Work proves [4] that the use of FeCl3 during reagent flotation with removal of resinous substances leads to a significant decrease in chemical consumption of oxygen (by 56.37 % at pH=9), which allws the authors to argue about the oxidation of a part of organic compounds to mineral
©
ones, which is significantly less harmful. The main disadvantage of the method is a difficulty connected with the disposal of flotation sludges, which are sources of pollution of the environment by heavy metal ions and polycyclic aromatic hydrocarbons (PAH).
We can achieve a simultaneous removal of resinous and suspended matter from wastewater even at very high initial concentrations (196 and 1,123 mg/dm3, respectively) due to the use of flocculants based on polyacrylamide. Rather high cost restrains large-scale use of flocculants. Although there are active developments on application of flocculants made of natural substances (chitosan, starch, lignin, etc.) [5].
World experience [6-11] in the development of new technologies for water purification contaminated with organic substances, which are capable of forming stable emulsions, proves the expediency of the use of various types of natural disperse minerals (bentonite, glauconite or paligrosite clays). Clays can be used both in natural form and after special activation (modification of clay surface with surfactants or special inorganic substances).
In the context of the study, the main scientific interest is the study of purification of waste water from organic compounds, which are similar to resinous substances in properties, in particular, PAH.
in the course of studies on adsorption of naphthalene from aqueous solutions with natural and bentonite-modi-fied hexadecyltrimethylammonium bromide (TTAB-Mt), paper [6] found that the latter is an effective sorbent of this substance, especially at pH equal to 4.00 and 5.97, respectively. Under conditions of a purification process at coke enterprises, such a low pH value is irrational (the reaction of the medium lies within the range of 7.3-8.3). The adsorption capacity of TTAB-Mt in relation to PAH decreases in the range of xylene>ethylbenzene>toluene>benzene [7]. It is naphthalene that defines physical and chemical properties of resins as the main component of an identified part of a chemical composition [8]. As a result of modification, the interlayer distance of a crystalline bentonite lattice expands from 1.152 nm to 2.175 nm [9], which increases a specific surface of particles of clay. During concurrent application of bentonite and TTAB modifier, along with the removal of PAH, we get binding of 90 % of phenols due to n-n interaction. The adsorption capacity of the modified bentonite is increased by 10 times, and the regeneration of the spent sorbent is almost 100 % [10].
Work [11] shows that there are inorganic modifiers located in the range of salt<alkali<acid according to a level of the increase in the adsorption activity of modified benton-ite in relation to naphthalene. Because acid-modified HCl bentonite significantly increases a specific surface area and total pore volume, it is considered a promising sorbent for purification of liquid media from PAH.
The listed methods of modification of bentonite presuppose a presence of appropriate modifying agents, which are very expensive. This circumstance limits the development of a use of activated bentonite sorbents substantially, especially in a case of large amounts of wastewater. Therefore, a special object of a scientific interest is a use of bentonite in a natural state, without modification. Paper [1] gives positive results obtained during purification of wastewater of coke plants from resinous substances using natural bentonite clay. But the paper uses empirical data for a description of the purification processes and does not reveal quantitative characteristics of flocculation and adsorption purification.
3. The aim and objectives of the study
The aim of present study is to reveal objective laws of processes of coagulation, flocculation and adsorption purification of wastewater of coke-chemical enterprises from resinous substances.
The achievement of the objective set involves solution of the following tasks:
- obtaining of dependences of the mass of sediment pollutant-containing aggregates of a dispersed phase on the time of sedimentation during coagulation, flocculation and adsorption purification of phenolic wastewater;
- calculation of a prevailing radius of pollutant-containing aggregates by the method of graphical processing of results of sedimentation analysis;
- determination of the most effective way to purify phenolic wastewater on the basis of a comparative analysis of the sedimentation rate and geometric sizes of pollutant-containing aggregates of different types.
4. Materials and methods of the study of wastewater of coke enterprises by the method of sedimentation analysis
4. 1. Substances and equipment used in the study
The study used phenolic wastewater from PJSC "Dneprovsky CCF" (Ukraine). The following indicators characterized the wastewater (Table 1).
Table 1
Physical and chemical characteristics of the phenolic wastewater under study
Characteristic Value
Resinous substances, mg/dm3 265
Suspended matter, mg/dm3 520
COD (chemical oxygen demand), mg(02)/dm3 4,800
Phenols, mg/dm3 500
pH 8.2
Density, kg/m3 993
Viscosity, mPa-s 0.774
Color Dark grayish brown
As we can see from Table 1, the content of the main pollutants in the studied wastewater corresponded the average regulatory content in the industry with a slight excess of the regulatory content of resinous substances [12]. During experiments, we maintained wastewater temperature at a temperature of 323±2 K in a thermostat (identical to industrial conditions). We determined the concentration of resinous substances in phenolic wastewater photometrically according to the methodology developed by the state enterprise "Ukrainian State Research Carbon Institute" (UCIN) No. 63.08.
We used technical aluminum hydroxy chloride Pol-vac-68 (TU U 19155069.001-1999) and ferrum (III) chloride (TU U 24.1-05444552-045-2005) as coagulants. The cationic flocculant was Extrafloc P70 product based on polyacrylamide produced by Open Joint-Stock Company PCF "Coagulant" (TU U 24.1-19155069-014-2011). We used bentonite clay with a mass fraction of alkaline metals (Na+K) at recalculation to their oxides of 3.9 %, with a true density of 2,199 kg/m3, manufactured by LLC "Filtr Prom Company" (TU U 320.00136751.032-1999).
The dosage of coagulants was 50 mg/dm3 of a main active substance (Al2(OH)5Cl and FeCl3, respectively) with an air supply intensity equal to 0.5 m3/m3 and a wastewater volume of 0.5 dm3. We mixed coagulants with wastewater pneumatically by bubbling of air through dispersants - glass filters of Schott No. 2. Duration of bubbling was 20 minutes, after which purified water and sludge became a subject to sedimentation analysis.
In the study of phenolic water flocculation with the use of Extrafloc P70 at a dosage of 4 mg/dm3, we applied Jar-Test method [13], according to which the stirring rate was 350 rpm during first 60 s, and 50-60 rpm within the next 20 minutes. After that, we stirred the purified wastewater again, together with a sediment, in a mode of 350 rpm for 15 s and poured it into a glass container with a height of 25 cm, which was located in a thermostat. We placed a cup of torsion scales into a tank with a suspension for 5 seconds at a depth of H=0.155 m. We measured the mass of sediment pollutant-containing aggregates at intervals of 15...60 s. We used VT-500 torsion scales of the III class of accuracy with a weighing limit of 0.5 g and an absolute error of ±10-3 g in the course of sedimentation analysis.
We carried out the adsorption study under static conditions in a reactor of 0.5 dm3 at a stirring rate of 250 rpm, with Extrafloc P70 flocculant at a dosage of 4 mg/dm3; a dosage of alkaline bentonite clay was 100 mg/dm3. The process of adsorption went until formation of a clearly visible sediment and clarification of phenolic water (from 1 to 3 minutes). After that, we subjected water together with the sediment of a total volume of 0.5 dm3 to sedimentation analysis using the above methodology.
We performed the regression analysis of the experimental data, the construction of diagrams and the calculation of reliability values of the approximation in the Microsoft Excel 2016 environment.
4. 2. Methods of data processing for sedimentation analysis
There were three forces, which influenced a spherical particle precipitated in a viscous medium: the gravity directed downward and two forces directed upwards: the strength of Archimedes and the strength of a viscous resistance (Stokes force). We can write the equation (1) describing the combined effect of mentioned three forces as follows [14]:
4nr3 4rcr3
Pg = Po g + 6nr nu,
(1)
after its transformation, we obtain the equation (2) for calculation of rate of a motion of pollutant-containing aggregates [14]:
. 2(p-p0)g r ' 9n '
equation (3) for calculation of a radius using the transformation of equation (2) [14]:
9nu
2(p-Po ) g'
(3)
We can simplify the equation (3) if we combine all stable under given conditions values in a constant K. As a result, we obtain the working equation (4):
-=k4U ,
(4)
where the rate of sedimentation of pollutant-containing aggregates u is equal to the ratio of a height H (m) to duration t (s) of sedimentation (we determined these values experimentally).
Based on the data obtained with the use of torsion scales, we construct a sedimentation curve - the dependence of the mass of pollutant-containing aggregates m, which precipitated, on the time of sedimentation t. Then we process the curve graphically to construct differential and integral curves for the distribution of pollutant-containing aggregates by sizes [14].
We calculate the density of the pollutant-containing aggregates on the basis of values of the density of a dry dispersed phase, taking into account its moisture content by the rule of addiction. We determine the moisture content of sediments gravimetrically by drying at a temperature of 105 0C to constant mass. Since values of the density and the viscosity of a dispersion medium remained almost unchanged during the use of different reagents, we determine the value of the constant K mainly by the dispersion phase density, which was determined by the picnometry method (Table 2).
Table 2
Dependence of values of constant K on the density of pollutant-containing aggregates
Indicator Al2(OH)5Cl FeCl3 Benton-ite clay Extrafloc P70 Bentonite clay+Extra-floc P70
Density of a dry solid phase, kg/m3 1,916 2,900 2,199 1,302 1,900
Moisture, mass fraction 0.65 0.46 0.56 0.68 0.63
Density, kg/m3 1,193 1,529 1,308 1,076 1,207
K-10-4 13.34 8.14 10.62 20.72 12.87
(2)
Thus, with an increase in the density of pollutant-containing aggregates formed with the use of different reagents, a value of the constant K decreases.
where u is the rate of aggregate sedimentation, m/s; p and p0 are the densities of a disperse phase and a dispersion medium, respectively, kg/m3; g is acceleration of gravity, m/s2; n is the viscosity of a dispersion medium, Pa-s; r is an equivalent radius of a spherical aggregate, m.
If characteristics of a dispersion medium (p0, n), a disperse phase (p) and rate of sedimentation of pollutant-containing aggregates of a disperse phase u are known, we obtain the
5. Results of the study on the process of purification of wastewater of coke-chemical enterprises by the method of sedimentation analysis
At the first stage of the study, we obtained sedimentation curves of the pollutant-containing aggregates of the dispersed phase of phenolic wastewater after purification by various methods. Fig. 1 shows the general view of curves.
40
ou 30
20
10
f 5 3
4
0 45 90 150 240 330 480 660 840 1140 r, s
Fig. 1. Dependence of the mass of sediment pollutant-containing aggregates of the dispersed phase m on the duration of the process t: 1 — coagulation with the use of A^OH^Cl at a dosage of 50 mg/dm3;
2 — coagulation with the use of FeCl3 at a dosage of 50 mg/dm3;
3 — adsorption of bentonite clay at a dosage of 100 mg/dm3; 4 — flocculation with the use of Extrafloc P70 at a dosage of
4 mg/dm3; 5 — adsorption of bentonite clay at a dosage of 100 mg/dm3 with the addition of Extrafloc P70 at a dosage
of 4 mg/dm3
Using equation (4) at a height of the immersion of a cup of torsion scales #=0.155 m for values of the constant K of pollutant-containing aggregates (Table 2), we constructed integral curves for the distribution of the dispersed phase of purified wastewater according to radii (Fig. 2-6).
60 80 r, (am
Fig. 2. Integral distribution curve of pollutant-containing aggregates of the dispersed phase of wastewater by radii after coagulation with the use of Al2(OH)5Cl at a dosage of 50 mg/dm3 [m=-0.0003/3+0.007/2-0.4837/+13.561]
15 20 25 30 35 40 45 r, (im
Fig. 3. Integral distribution curve of pollutant-containing aggregates of the dispersed phase of wastewater by radii after coagulation with the use FeCl3 at a dosage of 50 mg/dm3 [m=-0.0012/3+0.1154/2-3.8452/+45.331]
Experimental data show that sizes (Fig. 2-6) and density (Table 2) of pollutant-containing aggregates determine their sedimentation time. Fig. 1 shows this.
Differential distribution curves by radii presented in Fig. 7-11 give a clearer idea of the value of predominant content of pollutant-containing aggregates of the specified radii.
70 75 r, (am
Fig. 4. Integral distribution curve of pollutant-containing aggregates of the dispersed phase of wastewater by radii after flocculation with the use of Extrafloc P70 at a dosage of 4 mg/dm3 [m=-0.0007/3+0.1573/2-11.55/+291.32]
Fig. 5. Integral distribution curve of pollutant-containing aggregates of the dispersed phase of wastewater by radii after adsorption by bentonite clay at a dosage of 100 mg/dm3 [m=-0,0007/5+0,0786/4-3,2979/3+ +68,505/2-704,68/+2878,9]
Fig. 6. Integral distribution curve of pollutant-containing aggregates of the dispersed phase of wastewater by radii
after adsorption by bentonite clay at a dosage of 100 mg/dm3 with the addition of Extrafloc P70 at a dosage of 4 mg/dm3 [m=-0,0007/6-0,0003/5+0,0071/4--0,7587/3+45,055/2-1409,2/+18206]
0,05
0,04
0,03
0,02
0,01
0
29 31 35 40 49 63 70 83 96 r, (am
Fig. 7. Differential distribution curve of pollutant-containing aggregates of the dispersed phase of wastewater by radii after coagulation with the use of A^OH^Cl at a dosage of 50 mg/dm3
5 4 3
S < 2
18 20 22
24 27 r, |am
30 33
39
Fig. 8. Differential distribution curve of pollutant-containing aggregates of the dispersed phase of wastewater by radii after coagulation with the use of FeCl3 at a dosage of 50 mg/dm3
Fig. 9. Differential distribution curve of pollutant-containing aggregates of the dispersed phase of wastewater by radii after flocculation with the use of Extrafloc P70 at a dosage of 4 mg/dm3
16 20 r, |im
Fig. 10. Differential distribution curve of pollutant-containing aggregates of the dispersed phase of wastewater by radii after adsorption with bentonite clay at a dosage of 100 mg/dm3
Table 3
The content of resinous substances after purification by various methods
Purification method Concentration of resinous substances, mg/dm3
Initial In purified water
Coagulation with the use of Al2(OH)5Cl at a dosage of 50 mg/dm3 9
Coagulation with the use of FeC^ at a dosage of 50 mg/dm3 18
The use of Extrafloc P70 at a dosage of 4 mg/dm3 265 35
Adsorption by bentonite at a dosage of 100 mg/dm3 50
Adsorption by bentonite at a dosage of 100 mg/dm3 with the addition of Extra-floc P70 at a dosage of 4 mg/dm3 10
72 76 r, (am
Fig. 11. Differential distribution curve of pollutant-containing aggregates of the dispersed phase of wastewater by radii after adsorption by bentonite clay at a dosage of 100 mg/dm3 with the addition of Extrafloc P70 at a dosage of 4 mg/dm3
The main indicator of the efficiency of the investigated purification methods is the content of resinous substances in purified water. Table 3 presents the results of purification of phenolic water.
As we can see from Table 3, the content of resinous substances in purified wastewater is least when we use Al2(OH)5Cl and bentonite clay with the addition of Extrafloc P70. At the same time, when we use Al2(OH)5Cl, the sedimentation of pollutant-containing aggregates occurs very slowly (Fig. 1), and we do not observe the clarification of water due to the fact that dispersed aggregates of small density are usually formed (Table 2). When we use bentonite clay with the addition of Extrafloc P70, the size of pollutant-containing aggregates increases, which leads to a quick clarification of water (Fig. 1).
6. Discussion of results of sedimentation analysis of wastewater of coke-chemical enterprises
Turning to integral distribution curves of pollutant-containing aggregates of the dispersed phase (Fig. 2-6), it is necessary to emphasize their general similarity to each other and the absence of abnormal sections. We also should note that the starting point of mass distribution of pollutant-containing aggregates by radii is different in all cases. And this fact shows unevenness of aggregate contents per unit volume of wastewater in presence of various reagents. For example, we observed the highest content of pollutant-containing aggregates when we used bentonite clay (43 mg per 500 cm3 of phenolic water) with the addition of Extrafloc P70, which is the result of combined precipitation of bentonite clay and organic pollutants.
It is noteworthy that a significant (~80 s) reduction in the duration of sedimentation occurs at the simultaneous use of bentonite clay and flocculant (Fig. 1), which is well consistent with previous studies [1]. The reason for this phenomenon is the interaction of hydrophilic coagulants containing alkaline bentonite clay with Extrafloc P70 polymer structures, which leads to sediment formation with high sedimentation properties. A significant difference in the true density of bentonite clay and phenolic water also contribute this. The mechanism of the process is as follows: amide functional groups of cationic type of Extrafloc P70 bind to surface hydroxide bentonite groups due to forces of electrostatic interaction. As a result, there is the formation of larger pollutant-containing aggregates (flocculus).
Favorable temperature conditions accelerate the process also. The temperature of phenolic water is 323 K on
average. Data on sedimentation confirm aggregation. The most probable radius of pollutant-containing aggregates increases (Fig. 11). Extrafloc P70 binds particles not only to bentonite, but also to suspended matter, coke and other dispersed contaminants, which results in purification and clarification of phenolic water. At the same time adsorption of resinous substances by the surface of pollutant-containing aggregates of bentonite goes. The prevailing radius of pollutant-containing aggregates of the dispersed phase increases to 70...90 |m.
At the same time, the duration of sedimentation of the dispersed phase in the presence of bentonite clay is the longest (~20 min) because a suspension with the smallest radius of pollutant-containing aggregates is formed - 23...27 |im (Fig. 10) in this case.
The duration of sedimentation of the dispersed phase with the addition of Extrafloc P70 is 210 s only. There are units of a prevailing radius of 60...80 |im formed during it. That is, the deposition time correlates with sizes of pollutant-containing aggregates. At the same time, when using Extrafloc P70 only, the duration of sedimentation is greater than when using bentonite clay with the addition of Extrafloc P70 by 3.5 times. This is due to an increase in the prevailing radius from 60...80 |m to 70...90 |m (Fig. 9, 11). Even more reduction in the duration of deposition (by 15 times) occurs due to an increase in the prevailing radius from 23...27 |im in the presence of bentonite clay only, up to 70...90 |im with the addition of Extrafloc P70.
We should note that there is a significant difference in the sediment mass, which precipitates, at the same time intervals in the presence of various reagents ( Fig. 1). This mass exceeds all others by 2.5-8 times for bentonite+flocculant. This fact indicates the deposition of aggregated pollutant-containing aggregates with a large radius (70...90 |m) and observed intensive clarification of phenol water. The use of other methods of purification of phenolic waters applied in this study does not lead to clarification of water at all.
When using FeCl3 coagulant, an average size of pollutant-containing aggregates (Fig. 8) is 33...39 |m, which significantly reduces sedimentation rate of ferrum-containing aggregates. We assume that Fe(III) ions form more dispersed particles under such purification conditions. They have lower affinity with pollution of phenolic waters compared with other reagents. A high value (18 mg/dm3) of residual concentrations of resinous substances confirms this (Table 3).
Comparing the efficiency of removal of resinous substances by the use of different methods, we should take
into account that the maximum permissible concentration of such substances in purified water should be less than 25 mg/dm3 [1, 2]. Data from Table 3 shows that we can achieve a required degree of purification using coagulants Al2(OH)5Cl and FeCl3, as well as in processing with bentonite clay with the addition of Extrafloc P70. We should dive an advantage to the last of the methods, because the cost of bentonite clay in Ukraine today is 5-10 times lower than the cost of Al2(OH)5Cl or FeCl3. In addition, bentonite clay and flocculants, unlike coagulants, do not accelerate the development of corrosion of purifying equipment.
7. Conclusions
1. Sedimentation analysis of the disperse phase of purification of phenol wastewater showed that the integral rate of sedimentation of pollutant-containing aggregates is, mg/s: Al2(OH)5Cl at a dosage of 50 mg/dm3 - 0.017; FeCl3 at a dosage of 50 mg/dm3 - 0.024; Extrafloc P70 at a dosage of 4 mg/dm3 - 0.05; bentonite clay at a dosage of 100 mg/dm3 - 0.02; bentonite clay at a dosage of 100 mg/dm3 with the addition of Extrafloc P70 at a dosage of 4 mg/dm3 - 0.61. That is, the greatest rate of deposition is demonstrated by aggregates formed with the combined use of bentonite clay and flocculant.
2. As a result of the processing of sediment curves, we found that during the purification of phenolic waste-water, we get pollutant-containing aggregates of the following prevailing radii, |im: Al2(OH)5Cl at a dosage of 50 mg/dm3 - 30...90; FeCl3 at a dosage of 50 mg/dm3 -33...39; Extrafloc P70 at a dosage of 4 mg/dm3 - 60...80; bentonite clay at a dosage of 100 mg/dm3 - 23...27; bentonite clay at a dosage of 100 mg/dm3 with the addition of Extrafloc P70 at a dosage of 4 mg/dm3 - 70...90.
3. Comparative analysis of sedimentation rate and geometrical sizes of pollutant-containing aggregates shows that the most effective method for purification of phenolic wastewater of coke-chemical enterprises is the combined use of alkaline bentonite clay with a dosage of 100 mg/dm3 and a cationic flocculant Extrafloc P70 at a dosage of 4 mg/dm3. This method provides the largest integrated sedimentation rate of aggregates 0.61 mg/s and intensive water clarification in 1-3 min. In this case, we achieve a high degree of purification of wastewater from resinous substances - 96 %.
References
1. Klymenko, I. Developing of effective treatment technology of the phenolic wastewater [Text] / I. Klymenko, D. Yelatontsev, A. Ivanchenko, O. Dupenko, N. Voloshyn // Eastern-European Journal of Enterprise Technologies. - 2016. - Vol. 3, Issue 10 (81). -P. 29-34. doi: 10.15587/1729-4061.2016.72410
2. Ivanchenko, A. V. Researching the technology of tar removal from coke-chemical plants' wastewater by reagent flotation method [Text] / A. V. Ivanchenko, D. O. Yelatontsev, M. D. Voloshin, O. O. Dupenko // Odes'kyi Politechnichnyi Universytet. Pratsi. -2015. - Issue 1 (45). - P. 158-163. doi: 10.15276/opu.1.45.2015.26
3. Pat. No. 111944 UA. The method cleaning phenolic wastewater from coal tar. MPK C02F 1/24, B03D 1/02 [Text] / Yelatontsev D. O., Ivanchenko A. V., Voloshin M. D. - No. u201605987; declareted: 02.06.2016; published: 25.11.2016, Bul. No. 22.
4. Chaudhari, P. K. Treatment of coke oven effluent by coagulation process [Text] / P. K. Chaudhari, R. Chaudhary // International Journal of ChemTech Research. - 2016. - Vol. 9, Issue 3. - P. 640-644.
5. Lee, C. S. A review on application of flocculants in wastewater treatment [Text] / C. S. Lee, J. Robinson, M. F. Chong // Process Safety and Environmental Protection. - 2014. - Vol. 92, Issue 6. - P. 489-508. doi: 10.1016/j.psep.2014.04.010
6. Kaya, E. M. Ö. Adsorption kinetics and isotherm parameters of naphthalene onto natural- and chemically modified bentonite from aqueous solutions [Text] / E. M. Ö. Kaya, A. S. Özcan, Ö. Gök, A. Özcan // Adsorption. - 2013. - Vol. 19, Issue 2-4. - P. 879-888. doi: 10.1007/s10450-013-9542-3
7. Nourmoradi, H. Multi-Component Adsorption of Benzene, Toluene, Ethylbenzene, and Xylene from Aqueous Solutions by Montmorillonite Modified with Tetradecyl Trimethyl Ammonium Bromide [Text] / H. Nourmoradi, M. Khiadani, M. Nikaeen // Journal of Chemistry. - 2013. - Vol. 2013. - P. 1-10. doi: 10.1155/2013/589354
8. Pasternak, A. A. Dispersionnyy analiz nadsmol'nykh vod koksokhimicheskogo proizvodstva [Dispersive analysis of tarry wastewater in coke production] [Text] / A. A. Pasternak, N. Yu. Andreyev, V. P. Belonoshchenko, L. P. Bannikov // UgleKhimicheskiy zhurnal. -2013. - Issue 5. - P. 64-70. - Available at: http://nbuv.gov.ua/UJRN/ukhj_2013_5_14
9. Liu, D. M. Experimental Study of Organic Pollutants in Waste Water from the Coking Plant Adsorbed by Organobentonite [Text] / D. M. Liu, B. K. Jiang // Advanced Materials Research. - 2011. - Vol. 402. - P. 747-752. doi: 10.4028/www.scientific.net/ amr.402.747
10. Mirmohamadsadeghi, S. An efficient method for clay modification and its application for phenol removal from wastewater [Text] / S. Mirmohamadsadeghi, T. Kaghazchi, M. Soleimani, N. Asasian // Applied Clay Science. - 2012. - Vol. 59-60. - P. 8-12. doi: 10.1016/j.clay.2012.02.016
11. Owabor, C. N. Enhanced Sorption of Naphthalene onto a Modified Clay Adsorbent: Effect of Acid, Base and Salt Modifications of Clay on Sorption Kinetics [Text] / C. N. Owabor, U. M. Ono, A. Isuekevbo // Advances in Chemical Engineering and Science. -2012. - Vol. 02, Issue 03. - P. 330-335. doi: 10.4236/aces.2012.23038
12. Kirbaba, V. V. Nailuchshiye dostupnyye tekhnologii i ih vnedreniye na PAO «Avdeyevskiy koksokhimicheskiy zavod» [The best available techniques and their implementation at PJSC «Avdiivka Coke»] [Text] / V. V. Kirbaba, A. S. Malysh, A. L. Borisenko, N. I. Avilova, K. Ye. German // UgleKhimicheskiy zhurnal. - 2013. - Issue 5. - P. 83-89. - Available at: http://nbuv.gov.ua/UJRN/ ukhj_2013_5_17
13. Ismail, I. M. Combined coagulation flocculation pre treatment unit for municipal wastewater [Text] / I. M. Ismail, A. S. Fawzy, N. M. Abdel-Monem, M. H. Mahmoud, M. A. El-Halwany // Journal of Advanced Research. - 2012. - Vol. 3, Issue 4. - P. 331-336. doi: 10.1016/j.jare.2011.10.004
14. Frolov, Yu. G. Laboratornyye raboty i zadachi po kolloidnoy khimii [Laboratory work and tasks on colloid chemistry] [Text] / Yu. G. Frolov; Yu. G. Frolov, A. S. Grodskoy (Eds.). - Moscow: Khimiya, 1986. - 216 p.
