Performance of integrated process using fungal strain corialus versicalor mtc

International Journal of Advanced Research in Engineering and Technology (IJARET), ISSN 0976 –
6480(Print), ISSN 0976 – 6499(Online) Volume 4, Issue 6, September – October (2013), © IAEME
27
PERFORMANCE OF INTEGRATED PROCESS USING FUNGAL STRAIN
CORIALUS VERSICALOR (MTCC-138) IN MICROBIAL DYES
DEGRADATION
B. Chirsabesan and M.Vijay*
Department of Chemical Engineering, Annamalai University, Annamalai Nagar,
Chidambaram -608002, India
ABSTRACT
This work has been carried out for dyes degradation with the aim of investigating the effect
of fungal strain Corialus versicalor ((MTCC-138) and increase process understanding in order to
optimize the degradation reactions. From an applied experimentally based approach, membrane
assisted electrochemical degradation and bio degradation of Quinoline Yellow, Eosin B and Rose
Bengal dyes have been studied. The research was focused on using electrochemical equipment. . The
specific degradation rates obtained showed that Corialus versicalor much more efficient in the
decolourisation of dyes. This type of relation suggests that the decolourisation kinetics is energy-
dependent. The free fungi cells of Corialus versicalor has the ability to reduce the percentage of
COD more than 90% and to convert the effluent into reusable condition for the selected dye effluent
with the aid of electro chemical oxidation at the specified conditions
Key words: Corialus versicalor, Quinoline Yellow, Eosin B, dye degradation efficiency, current
efficiency.
1. INTRODUCTION
The process of biodegradation can be measured by monitoring any of the two factors, (1) by
measuring the redox potential, together with pH and temperature, oxygen content and concentration
of electron acceptors/donors as well as breakdown products such as carbon dioxide etc. (2)
Measurement of chemical oxygen demand (COD) and biological oxygen demand (BOD). Biological
oxygen demand represent only the organism matter which is being capable of degraded/oxidized by
microbes where as COD represents all the oxidizable matters including organic matter in any
particular effluent. In case of colored effluents, bioremediation is measured by estimating the
decrease in color intensity. (Marmagne and Coste, 1996).
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Although it is thought that some dyes are nearly non-biodegradable or un transformable by
bacteria under aerobic condition, efforts to isolate bacteria capable of degrading dye have continued.
Hu (1998) isolated Pseudomonas luteola from waste water treatment plant that decolorize reactive
azo dyes. Wong and Yuen (1996) isolated a bacterium Klebsiella pneumoniae from dye
contaminated sludge that could degrade the methyl red up to 100 mg l-1 more efficiently than other
isolated bacteria.
The ability of two bacterial strains, the Gram-negative Alcaligenes faecalis and the Gram-
positive Rhodococcus erythropolis to decolorize the monoazo dye Acid orange were studied with
different initial dye concentrations by Mutafov et al. (2007). The azo dye and Reactive yellow 84A
was efficiently degraded by a novel bacterial strain Exiguobacterium sp. White rot fungi can
decolorize and degrade wide variety of azo dyes with the help of extracellular degradative enzymes.
White rot fungi that produce lignolytic enzymes, such as lignin peroxidase, manganese peroxides and
laccase have been studied extensively because of their ability to degrade various organic compounds
(Fu and Viraraghvan, 2001)Decolorization of dyes normally begins with initial reduction cleavage of
functional bond anaerobically, which results in colorless but toxic aromatic amines. This is followed
by complete degradation of dyes under aerobic conditions. Therefore, anaerobic/aerobic processes
are crucial for complete mineralization of organic dyes. However, not all bacteria have both
anaerobic and aerobic properties. Usually consortia are routinely used for the degradation of azo
dyes.
Recent research has exposed the survival of wide variety of organisms in mixed culture
capable of decolorizing a wide range of dyes. The complexity of the microbial consortium enables
them to act on a variety of pollutants. Microbial consortia are usually used without analyzing the
constituent microbial populations for environmental remediation (Mohorcic et al., 2004). Many
reports indicate that textile industry effluent have toxic effect on the germination rates and biomass
concentration (Wang, 1991). The toxicity of effluent is because of the presence of dye or its partially
degraded product which are mutagenic or carcinogenic. Therefore the treatment of organic textile
dyes becomes necessary prior to their final discharge to the environment (Kumar and Dastidar,
2009).
Membrane-wet oxidation, an integrated process, has been demonstrated by Dhale and
Mahajani (2000) to treat the disperse dye bath waste. On the other hand, these techniques do not
eliminate definitively the dyes but only separate and concentrate them. The destruction of the
concentrated pollutants requires an additional operation as incineration. However, as yet, there has
not been a method employing the electrochemical oxidation process combined with the membrane
filtration process for the treatment and reuse of textile dyehouse wastewater. The goal of this
research is to study the performance of the arc-shaped transfer-flow membrane module, at the same
time, to demonstrate these processes and to develop a potential dye wastewater treatment system for
reuse
The present study deals with studies on the Quinoline Yellow, Eosin B and Rose Bengal dyes
decolorization by individual fungaistrains as well as membrane assisted electro chemical oxidation.
Assessment of the removal efficiency of Quinoline Yellow, Eosin B and Rose Bengal dyes as well as
its degradative capacity was also carried.
2. MATERIALS AND METHODS
Analytical grade reagents of NaOH, Na2CO3, K2Cr2O7, H2SO4, Na2SO4, CH3OH, KBr,
ferrous ammonium sulfate, ethyl acetateare used for all the analysis. Textile dye Quinoline Yellow,
obtained from pollution control division, Central Electrochemical research Institute, Karaikudi,
Tamilnadu. PES (3500) was received from Udel. Rose Bengal (C20H2Cl4I4Na2O5, Mr: 1017.65) was

29
procured from M/S Merck and the 0.01 M stock solution was the dye was prepared in doubly
distilled water.
Eosin B dye (4´,5´-Dibromo- 2´,7´dinitrofluorescein di sodium salt, colour index: 45400),
chloroform, chlorosulfonic acid,methanol, and dimethylformamide (AR grade) were obtained from
S.D fine Chemicals, India, and were used without any further purification. Fungal strain Corialus
versicalor ((MTCC-138) was obtained from microbiology laboratory, Bharathidasan University,
Trichy and used for the study.
2.1. Dye Effluent Preparation
Dye concentration selected for experiments was 200 mg/L. This value is included in the
range of real dye concentration found in textile effluents. Synthetic Quinoline Yellow, Eosin B and
Rose Bengal dye bath effluent used in the present study was prepared according to the composition
commonly used in cotton dyeing. In order to dye 0.1kg of fabric, 0.004 kg of dye is used. It is
dissolved in 1 L of double distilled water along with the auxiliary chemicals such as 0.003 kg
Na2CO3, 1 mL of NaOH 38°Bé (441×10-3
kgm-3
NaOH solution)and0.01kg of NaCl. A 1.0.10-3 M
solution of Rose Bengal was prepared as a stock solution, which was diluted further as and when
required. The optical density of the Rose Bengal solution was determined using a spectrophotometer
(Systronics model 106) at λmax = 550 nm.
2.2. Fungi Preparation
10mm Corialus versicalor ((MTCC-138) was taken from a fungal colony growingon potato
dextrose plates and inoculated into 500 ml Erlenmeyerflasks with 100 ml N-limited medium. The
flasks wereincubated statistically at 28°C and flushed with pure oxygendaily for the study of laccase
production. Fungai activitiesin the supernatant were determined at regular intervals.Unless otherwise
indicated, carbon source, nitrogensource and inducers were added to the N-limited mediumto study
their effects on laccase production.
2.3. Sulfonation of poly (ether ether ketone)
The sulfonation of PEEK (Victrex PEEKTM
450PF powder) was prepared using concentrated
sulfuric acid according to the following procedure.
2.3.1 Preparation of sulfonated poly (ether ether ketone)
The 20 g of PEEK was dried in a vacuum oven at 100o
C and then dissolved in 500 ml of
concentrated (95-98% H2SO4) sulfuric acid at 50-70o
C under vigorous mechanical stirring. The
reaction time ranged from 5 to 6 h. The sulfonation reaction was terminated by decanting the
polymer solution into a large excess of ice-cold water under continuous mechanical agitation and the
polymer precipitate was filtered and washed several times with distilled water until the pH was
neutral. The recovered SPEEK was dried at room temperature for 2 days, finally the polymer was
dried in a vacuum oven at 80°C for 24 h, and stored in a decicator (Jin et al 1985).

International Journal of Advanced Research in Engineering and Technology (IJARET), ISSN 0976
6480(Print), ISSN 0976 – 6499(Online) Volume 4, Issue
Table 1: Chemical structure of organic dyes
2.3.2. Characterization of sulfonated poly (ether ether ketone)
The sulfonated sample was characterized for functional group determination by FT
Spectroscopy and Nuclear magnetic resonance (NMR) spectra.
Perkin-Elmer, model-Spectrum RX1 Fourier transform spectrometer either with powder samples
inside a diamond cell or by using KBr pellets composed of 50 mg of IR spectroscopic
1mg polymer sample.
2.3.3.Preparation of Membranes
SPEEK membrane was prepared by the “diffusion induced phase separation” method,
namely, casting a thin film of the polymeric solution on a glass plate and, after allowing the solvent
to evaporate for a predetermined period at the desired humidity and temperature conditions,
immersing it into a bath of non-solvent (water, solvent, surfactant) for final precipitation. Prior to
membrane casting, a gelation bath of 2L of distilled water (non
(Solvent) and 0.2% SLS (Surfactant) was prepared and cooled to 10°C.
2.3. Analytical methods
The analytical methods used for this study are described below.
C.I.(Color Index)
CAS registration
number
Quinoline Yellow
Colour Index No.:
47005
Eosin B (disodium
salt)
CI Number: 45400
Rose bengal (disodium
salt)
CI Number: 45440
6499(Online) Volume 4, Issue 6, September – October (2013), © IAEME
30
le 1: Chemical structure of organic dyes
Characterization of sulfonated poly (ether ether ketone)
The sulfonated sample was characterized for functional group determination by FT
Nuclear magnetic resonance (NMR) spectra. FT-IR spectra were recorded on a
Spectrum RX1 Fourier transform spectrometer either with powder samples
inside a diamond cell or by using KBr pellets composed of 50 mg of IR spectroscopic
e for a predetermined period at the desired humidity and temperature conditions,
solvent (water, solvent, surfactant) for final precipitation. Prior to
membrane casting, a gelation bath of 2L of distilled water (non-solvent), containing 2% DMF
(Solvent) and 0.2% SLS (Surfactant) was prepared and cooled to 10°C.
The analytical methods used for this study are described below.
Chemical Structure
October (2013), © IAEME
The sulfonated sample was characterized for functional group determination by FT-IR
IR spectra were recorded on a
Spectrum RX1 Fourier transform spectrometer either with powder samples
inside a diamond cell or by using KBr pellets composed of 50 mg of IR spectroscopic grade KBr and
e for a predetermined period at the desired humidity and temperature conditions,
solvent (water, solvent, surfactant) for final precipitation. Prior to
, containing 2% DMF

6480(Print), ISSN 0976 – 6499(Online) Volume 4, Issue
2.3.1. Chemical Oxygen Demand (COD)
In order to determine the extent of degrad
(COD) was measured. The COD as the name implies is the oxygen requirement of a sample for
oxidation of organic and inorganic matter. COD is generally considered as the oxygen equivalent of
the amount of organic matter oxidizable by potassium dichromate. The organic matter of the sample
is oxidized with a known excess of potassium dichromate in a 50% sulfuric acid solution. The excess
dichromate is titrated with a standard solution of ferrous ammonium sulfate. COD
were determined by the dichromate closed reflux method using thermo reactor TR620
COD measurement, 3 samples are subjected to analysis for one COD data. From that, any two same
values or the average of any two nearer values is cons
2.3.2. Spectral analysis using UV-visible spectrophotometer
For UV-Visible spectral analysis, 5 mL of treated and untreated samples were taken and
centrifuged at 12,000 rpm for 10 min. The supernatant of untreated and treated
analyzed by monitoring the changes in its absorption spectrum using UV
with a cell having 1 cm optical path length.
3. RESULTS AND DISCUSSION
3.1. Characterization of sulfonation of poly (ether ether ketone)
The modification of polymers from hydrophobic in nature to hydrophilic is done by
introducing polar groups on polymer backbones. Chemical modification of polymers is also used in
many other applications to improve chemical resistance, enhance wear resistance and o
Sulfonation of Poly (ether ether ketone) was preferred as a way to introduce polar groups (sulfonic
acid groups) on this polymer. The introduction of sulfonic acid groups per repeating unit in the
PEEK chain leads to an increase in its solubility. S
PEEK, reduces the crystallinity and consequently affects solubility. The SPEEK could readily be
dissolved in solvents that are not solvents for the original PEEK, such as DMF, acetone and NMP.
Figure 1. Conformation of sulfonation
1655 cm-1
6499(Online) Volume 4, Issue 6, September – October (2013), © IAEME
31
2.3.1. Chemical Oxygen Demand (COD)
In order to determine the extent of degradation of the effluent Chemical Oxygen Demand
matter oxidizable by potassium dichromate. The organic matter of the sample
dichromate is titrated with a standard solution of ferrous ammonium sulfate. COD
were determined by the dichromate closed reflux method using thermo reactor TR620
values or the average of any two nearer values is considered as the measured data.
visible spectrophotometer
Visible spectral analysis, 5 mL of treated and untreated samples were taken and
centrifuged at 12,000 rpm for 10 min. The supernatant of untreated and treated
analyzed by monitoring the changes in its absorption spectrum using UV–visible spectrophotometer
with a cell having 1 cm optical path length.
RESULTS AND DISCUSSION
3.1. Characterization of sulfonation of poly (ether ether ketone)
fication of polymers from hydrophobic in nature to hydrophilic is done by
many other applications to improve chemical resistance, enhance wear resistance and o
PEEK chain leads to an increase in its solubility. Sulfonation modifies the chemical character of
nformation of sulfonation - Infra-Red Spectroscopy
1081 cm-1
1253 cm-1
1025 cm-1
709 cm-1
October (2013), © IAEME
ation of the effluent Chemical Oxygen Demand
matter oxidizable by potassium dichromate. The organic matter of the sample
dichromate is titrated with a standard solution of ferrous ammonium sulfate. COD of all samples
were determined by the dichromate closed reflux method using thermo reactor TR620-Merck.In
Visible spectral analysis, 5 mL of treated and untreated samples were taken and
centrifuged at 12,000 rpm for 10 min. The supernatant of untreated and treated samples were
visible spectrophotometer
fication of polymers from hydrophobic in nature to hydrophilic is done by
many other applications to improve chemical resistance, enhance wear resistance and others.
ulfonation modifies the chemical character of
Red Spectroscopy

32
The comparative FT-IR spectra of PEEK and SPEEK samples are shown in Figures 3.1 and
3.2. The broadband in SPEEK samples appearing at 3440 cm-1
was assigned to O-H vibration from
solfonic acid groups. The aromatic C-C band at 1489 cm-1
for PEEK was observed to split due to
new substitution upon sulfonation. A new absorption band at 1080 cm-1
in SPEEK was assigned to
sulfur-oxygen symmetric vibration O=S=O. The new absorption at 1245, 1080 and 1020 cm-1
, which
appeared upon sulfonation were assigned to the sulfonic acid group in SPEEK (Ahmed et al 2012
and Mayahia et al 2013).
3.2. Physico-chemical characterization of dye samples
The color, temperature and pH of the sample were recorded on the site and samples were
transported to the laboratory by storage at 4°C. Other physico-chemical characteristics like BOD,
COD, etc. were measured on the same day of collection of sample. The same integrated
electrochemical and biological oxidation method was used to degrade the simulated effluent
containing bio recalcitrant synthetic dye with a well established fungal strain Corialus versicalor. In
batch electro membrane reactor, electrochemical oxidation was carried out as a pretreatment before
the biodegradation cycles to increase biodegradability and at the end as a post treatment to meet the
required standards.
Table 2. Performance of integrated process using free fungal strain Corialus versicalor (MTCC-
138) in microbial degradation
Parameters and Operating
Conditions
Units Environment I Environment II
Batch Reactor holdup mL 200 200
Initial COD mg L-1
2300 2300
Electrochemical Mediated Oxidation Cycle I
Charge input Ah L-1
8 8
COD (after EMR with SPEEK
membrane )
mg L-1
1800 1800
Biochemical oxidation Using Corialus versicalor ((MTCC-138)
Inoculums input mL L-1
50 100
COD (after inoculum addition) mg L-1
1900 2150
COD (after 120 h of aerobic oxidation) mg L-1
1450 1310
Electrochemical Mediated Oxidation Cycle II
Charge input Ah L-1
4 4
membrane)
mg L-1
1220 1150
Inoculum input mg L-1
25 25
1300 1217
720 680
Electrochemical Mediated Oxidation Cycle III
Charge input Ah L-1
2 2
membrane)
mg L-1
670 626
Inoculums input mL L-1
25 25
765 715
480 379
Post EMR with SPEEK membrane mg L-1
240 194
Overall COD Removal (%) 90.6 92.4

33
Biological oxidation was carried out in 3 cycles for two different initial inoculum
concentrations at aerobic condition. In order to remove the microorganisms from the treated effluent
and bringing the effluent to reusable form, photo oxidation method was carried out. The results are
presented in the Figures 1 to 3 and Table 2. In 30 minutes of pretreatment of electro oxidation, it was
observed that the COD decreased from 2300 mg L-1
to 1800 mg L-1
(22% reduction) for the applied
charge of 1.6 Ah. This was found almost identical for all electro oxidation steps in different cycles,
as well for post electro oxidation and all other electrolysis steps.
Figure 2: Variation of %COD of Remeoval of Quinoline Yellow dye with time in 3 cycles for
degradation of Corialus versicalor
Biodegradation process was a sequential one and it was carried out under both aerobic and
anoxic conditions in two cycles of operation as indicated in Figure 1 to 3 for all dyes at 20 mL of
inoculum containing Corialus versicalor ((MTCC-138). These Figures clearly indicate that there are
remarkable changes in the course of the degradation process by Corialus versicalor by biochemical
reaction. The COD reduction obtained for two degradation conditions (aerobic and anoxic) were
21% and 24% in first cycle and 36% and 23% in second cycles respectively for the effluent
containing 20 mL of inoculum as observed from the Figure 1. Similarly from Figure 5.39 the COD
reduction obtained for two degradation conditions (aerobic and anoxic) as 27% and 47% in first
cycle and 30% and 23% in second cycle for the effluent containing 20 mL of inoculum respectively.
0
5
10
15
20
25
30
35
40
45
50
55
60
65
70
0 20 40 60 80 100 120 140 160
%ofCODRemeovalQuinolineYellow
Time (min)
Aerobic cycle I
Anoxic Cycle I
Aerobic Cycle II
Anoxic Cycle II

34
Figure 3:Variation of %COD of Remeoval of Eosin B dye with time in 3 cycles for degradation
of Corialus versicalor
From Figure 3, the COD reduction obtained in the first degradation environments were
26.9% in the first cycle and 44.6% in the second cycle in aerobic and anoxic cycle respectively for
the Eosin B dye effluent containing 20 mL of inoculums. Similarly from Figure 5.39 the COD
reduction obtained for second degradation environments were 37.6% in the first cycle and 44.1% in
the second cycle respectively for the rose Bengal dye effluent containing 20 mL of inoculums. As
presented in Table 3, the overall % COD reduction obtained in the integrated process treatment of
effluent containing dyes together with post electro membrane oxidation for the effluent containing 20
mL of inoculum is 92.4. The contribution of every stage and individual processes in integrated
scheme for total COD reduction based on initial inoculum size of biodegradation. Though both the
degradation environments gave almost identical total % COD reduction at the end of the integrated
process, it can be seen that increase in molecular weight of dyes (375.3, 580.09 and 1017.64) could
decrease %COD reduction up to 5% in biodegradation stages.
0
5
10
15
20
25
30
35
40
45
50
55
60
0 20 40 60 80 100 120 140 160
%ofCODRemeovalEosinB
Time (min)
Aerobic cycle I
Anoxic Cycle I
Aerobic Cycle II
Anoxic Cycle II

35
Figure 4.Variation of %COD of Remeoval of Rose Bengal dye with time in 2cycles for
degradation of Corialus versicalor
The initial % COD removal of dyes was 3% at 30 minutes. As shown in the Figure 3, % COD
removal increased and degraded in both process at 12 V of external potential supply. It is interesting
to note that when both electrochemical membrane reaction and biodegradation were used effectively.
This value is higher than the summation of the electrochemical and biodegrading process acting
alone. In other words, the contribution of both processes has resulted in an increase of degradation by
nearly 62.5%. Or the presence of both Corialus versicalor and PEM has enhanced the degradation by
37%. Such a synergetic effect between electro membrane reactor and bio degradation has been
recognized by Luca et al. [5] at Nafion membrane and fungi using degradation of dyes. Conventional
electrochemical process, electrolyte plays a very important role in the integrated photo-
electrochemical process. As anions of the supporting electrolyte may participate in the
decomposition reaction of dyes careful selection ofelectrolyte is essential in maximizing the
degradation rate of given compound and minimizing the formation of toxic intermediates. Sodium
chloride may electrochemically convert to chlorine, which may further react with intermediates to
produce polychlorinated compounds.
Comparatively, electro membrane reactor values are higher contribution than Bio degradation
for Quinoline Yellow. However, bio degradations are higher contribution than electro membrane
reactor in case of Eosin B dye solution. The reason is that Quinoline Yellow dye having low
molecular weight of organic material capable of being oxidized, while the COD represents a more
complete oxidation includes waste compounds that are difficult to breakdown with bacteria or
compounds that are completely non-biodegradable.
The membrane assisted electrochemical degradation method and biodegradation ismore
suitable to be applied in final stage of wastewater treatment where effluents have undergone pre-
treatment. Thus, membrane assisted electrochemical process should be used to complement the
conventional methods such as coagulation flocculation and biological treatment to ensure complete
mineralisation of the textile wastewater.
0
5
10
15
20
25
30
35
40
45
50
55
60
0 20 40 60 80 100 120 140 160
%ofCODRemeovalofRosebengal
Time (min)
Aerobic cycle I
Anoxic Cycle I
Aerobic Cycle II
Anoxic Cycle II

36
3.3. Modified Integrated Dye Degradation Process for dyes
In this study, a modified combination method has been tried to treat the synthetic effluent
containing Quinoline Yellow and Rose Bengal dye.
Table 3. Contribution of every stage and individual processes in integrated scheme when
Corialus versicaloris used in microbial degradation
Stage
Contribution of Dyes at 20mL inoculums
Quinoline Yellow Eosin B
(disodium salt)
Rose bengal
(disodium salt)
EMR – Cycle I 31.26 30.65 28.4
Bio degradation– Cycle I 16.93 19.98 20.5
EMR – Cycle II 10.36 8.85 9.85
Bio degradation – Cycle II 20.73 19.94 11.5
EMR – Cycle III 2.16 2.29 2.5
Bio degradation – Cycle III 8.20 10.46 9.56
Post EMR 10.36 7.83 5.67
Contribution of Individual processes
Electrolysis 54.15 49.62 45.6
Bio degradation 45.85 50.38 53.45
The prepared dye effluent was sequentially fed in to electrochemical membrane reactor for 4
h followed by different microbial batch reactors at aerobic conditions using fungal strains (Corialus
versicalor) and then again electrochemical membrane reactor for 5 h in sequence
3.4. Electrochemical Pretreatment
Due to 4 h of pre electro oxidation, COD of the effluent reduced from 2556 mg L-1
to
1370 mg L-1
(46%) for the applied charge of 3.84 Ah. The greater %COD reduction inmicrobial
oxidation may be obtained by increasing the degradation time in pre electrochemical methods to
enhance the biodegradability.
3.5. Microbial Oxidation
Microbial oxidation using two fungal strains were carried out for 120 h for the
electrochemically pre treated dye effluent. The results are shown in Table 4. The COD of the effluent
reduced for the increasing degradation time for all the micro organisms. At the end of 120 h, the
maximum COD reductions obtained was 33%, for the effluent containing both bacterial strain
Corialus versicalor.
It can be noted from Table 5.7, at the end of 4 h of pre electro membrane oxidation, COD of
the initial effluent was reduced from 2305 mg L-1
and 2350 for Quinoline Yellow and Rose Bengal
dye. The value reduced to 1370 mg L-1
and 1830 for respective dyes for the applied charge of 3.84 Ah
in PEM (SPES and SPEEK) membranes. In addition of 50 mL of inoculum (broth containing
bacterial strain) to 150 mL of effluent the COD value is increased in the entire stream due to
presence of biomass and its growth. In case of the fungi strain, Corialus versicalor, the COD value
increases from 1370 mg L-1
to 1734 mg L-1
due to the increase in bacterial concentration, and it
reduced to 1340 mg L-1
due to 120 h of biochemical oxidation, while the Rose Bengal dyeis
considered, the COD value increases from 2150mg L-1
for Corialus versicalor.

37
Table 4. Performance integrated process using fungal strains in microbial degradation
Parameters and Operating
Conditions
Units Environment
Pollutant Quinoline Yellow Rose Bengal dye
Initial COD mgL-1
2305 2350
Electrochemicalmembrane Pre treatment
Batch Reactor holdup mL 400 400
Charge input AhL-1
9.6 9.6
COD (after Electro Oxidation) mgL-1
1370 1830
Biochemical oxidation
Fungi Corialus
versicalor
R. arrhizus Corialus
versicalor
R. arrhizus
Effluent Volume mL 200 200 200 200
Inoculums Volume mL 50 50 50 50
Batch Reactor holdup mL 300 300 300 300
COD (after inoculum
addition)
mgL-1
1340 3500 1650 2150
COD (after 120 h of
aerobic oxidation)
mgL-
1
1026 1734 1225 952
Electrochemical MembranePost treatment
Charge input AhL-1
12 12 12 12
COD (after Electro
Oxidation)
mgL-1
580 420 640 360
Photo catalytic oxidation
COD (after Electro
Oxidation)
mgL-1
215 153 280 160
Overall COD Reduction
(%)
91.8 94.2 95.4 93.8
and it reduced to 1650 for Corialus versicalor due to growth of biomass and after 120 h of
biochemical oxidation it reduced from to 1225 mgL-1
and 952. Increased biomass concentration is
responsible for effective degradation.
3.6. Post Electrochemical membrane Oxidation
The biologically treated effluent streams subjected to electro chemical membrane oxidation
for 5 hours. The % COD reduction increases when time proceeds, for all effluent streams as shown
in Table 5.8. The maximum COD reductions obtained at the end of 5 h for the effluent streams
incubated with the fungi strain Corialus versicalor, in biochemical oxidation. The minimum COD
reduction of 19% was observed for the effluent incubated with the fungal strain Corialus versicalor.
3.7. Photo catalytic oxidation
The electro chemically treated effluent streams were subjected to membrane and photo
cataylytic oxidation for 5 h. The observed results are shown in Table 4. The %COD reduction

38
increases when time proceeds for all effluent streams. The maximum COD reductions obtained at the
end of 5 h of photo catalytic oxidation are COD of the effluent reduced from 580 mg L-1
to 215 mg
L-1
and COD of the effluent reduced from 640 mg L-1
to 280 mg L-1
for the effluent streams incubated
with the fungal strain Corialus versicalor for Quinoline Yellow in microbial oxidation respectively.
According to earlier reports of Alinsafi et al. (2007), Konstantinou and Albanis (2004), Neelavannan
et al. (2007) and Neelavannan and Ahmed Basha (2007), when TiO2 is illuminated by light (λ <390
nm) electrons are promoted from the valence band to the conduction band to give electron-hole pairs.
3.8. Overall % COD Reduction in Different Treated Effluent Streams
The overall COD reductions obtained at end of the sequential study for the different effluent
streams containing dye Quinoline Yellow and Rose Bengal dye are 91.8% and 95.4% for
respectively to the effluent streams containing fungal strain Corialus versicalor. The reductions
values of 94.2%, and 93.8% in COD were obtained for the Rose Bengal dye effluent streams
incubated with the fungal strain Corialus versicalor in microbial oxidation.
CONCLUSION
The dye stuffs and dye waste water from textile industry has created environmental pollution
as well as medical and aesthetic problems associated with human health and agriculture, thus
bioremediation of contaminated site is of prime importance. The difference in decolorization
capacity of different organic dyes by fungi was due to dissimilarity in specificities, structure and
complexity, and the interaction with functional bond with different dyes. Such biological processes
could be adopted as apre-treatment decolorization step, combined withmembrane assisted electro
oxidation and biological process to reduce the BOD and COD, as an effective alternative for use by
the textile-dyeing industries. The techniques by which decolorization occurs vary and among them
biodegradation seems of great significance for future development in bio-removal or bio-recovery of
dye substances
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