Potential of corn husk leaves for the co removal of phenol and cyanide from waste water using simultaneous adsorption and biodegradation

IJRET: International Journal of Research in Engineering and Technology eISSN: 2319-1163 | pISSN: 2321-7308
_________________________________________________________________________________________
Volume: 03 Issue: 02 | Feb-2014, Available @ http://www.ijret.org 700
POTENTIAL OF CORN HUSK LEAVES FOR THE CO-REMOVAL OF
PHENOL AND CYANIDE FROM WASTE WATER USING
SIMULTANEOUS ADSORPTION AND BIODEGRADATION
Priya Sengupta1
, Chandrajit Balomajumder2
1
Research Scholar, Department of Chemical Engineering, IIT Roorkee, Roorkee, Uttarakhand, India
2
Associate Professor, Department of Chemical Engineering, IIT Roorkee, Roorkee, Uttarakhand, India
Abstract
Application of biosorbents has gained a great importance in the present scenario of waste water purification. The present work
concentrates on the potential of biosorbent, Corn husk leaves, for the co-removal of phenol and cyanide from coke waste water by
simultaneous adsorption and biodegradation (SAB). The microbe used in the present study is the bacteria of Serratia Sp. The entire
SAB process was carried out at 30 0
C and for 60 h. Theoptimum process parameters i.e. pH, initial concentration of both phenol and
cyanide, adsorbent dose of corn husk leaves were analysed and their impact on the entire process were also studied. At the range of
initial concentration of phenol between 100-1000 mg/L and cyanide between 10-100 mg/L, the optimum pH was obtained between 6.5-
7 and an optimum adsorbent dose of 6 g/L. Multicomponent adsorption isotherms applied were Non-modified Langmuir, Modified
Langmuir, Extended Langmuir and Extended Freundlich. Out of the four isotherms applied non-modified Langmuir isotherm proved
to be the best fit for phenol and modified Langmuir isotherm was found to be best fit for cyanide. Phenol showed a removal
percentage of 75 % by SAB process and cyanide showed a removal percentage of 83 %. The data was also non-linearly modelled for
kinetic studies. Kinetic studies revealed that for both phenol and cyanide simultaneous adsorption and biodegradation took place by
physisorption as well as by chemisorption. Surface diffusion is dominating for the simultaneous adsorption and biodegradation of
phenol whereas in case of cyanide intraparticle diffusion is the dominating factor.
Keywords: biosorbents, corn husk leaves, simultaneous adsorption and biodegradation, optimum.
---------------------------------------------------------------------***---------------------------------------------------------------------
1. INTRODUCTION
Phenolics are organic compounds discharged in waste water
from different industries like insecticides, pesticides, textile,
dye, pulp and paper, iron and steel industries [1]. Phenols in
the environment are highly toxic to humans in their short term
or long term exposure. Exposure to phenol causes
gastrointestinal disorders, vomiting, depression and even death
[2]. Cyanides are a group of chemicals that have the –CN
bond. These inorganic compounds are discharged from
industries like mining, electroplating, iron and steel industries
[3]. Cyanide exposure also causes heart problems, breathing
disorders and even death (Cyanide Uncertainties). Phenols
and Cyanides are also listed in CERCLA priority list of
hazardous substances[4]. There are a couple of methods to
reduce the phenol and cyanide concentration in industrial
discharge to its MCL (Maximum Contaminant Level) which is
0.5 mg/L and 0.2 mg/L for phenol and cyanide respectively
[5,6]. Simultaneous adsorption and biodegradation of toxic
pollutants is one of the developingtechniques for purification
of waste water [7]. This process has an advantage of
simultaneous bed regeneration along with its being cost
effective [8]. The use of biosorbents has become much
prominent in the present times. Biosorbents or simply the
agricultural waste are easily available, the process is cost
effective and they have proved to be quite efficient in the
removal of toxic compounds from waste water [9].
The authors in this study have considered corn husk leaves as
an adsorbent and Serratia Sp. Bacteria as the microbe for
simultaneous adsorption and biodegradation of phenol and
cyanide. The operating parameters i.e. pH, adsorbent dose,
initial concentration were also optimized and the data obtained
was non linearly modeled for different adsorption isotherms
and kinetic models.
2. MATERIALS AND METHODS
2.1 Chemicals and Adsorbents
All the chemicals used in this study were of analytical grade
and obtained from Himedia Laboratories Pvt. Ltd. Mumbai
India. 0.189 g of NaCN was dissolved in 1L of millipore water
(Q-H2O, Millipore Corp. with resistivity of 18.2 MX-cm) to
prepare a stock solution of cyanide concentration of 100 mg/L.
The pH of the cyanide stock solution was adjusted to 10 using
1 N NaOH. The phenol stock solution, with the concentration
of 1000 mg/L, was prepared by adding 1 g of pure phenol

_________________________________________________________________________________________
crystals to 1 L of millipore water. Finally a binary mixture
stock solution of 1000 mg/L phenol and 100 mg/L cyanide
was prepared by the individual stock solutions.
Waste corn caps were collected from local shops. The fibers
were removed from the corn caps. The Corn husk leaves
obtained after removal of the fiber the caps were washed twice
with tap water to get rid of the dirt particles. The husk leaves
were then washed twice with Millipore water. After that the
husk leaves were dried at 50 0C for 24 h. When the leaves
were completely dried they were crushed to a size of 1.7 mm.
Thepercentage of ash and moisture in the adsorbent is 5.702
and 12.95 respectively as obtained by proximate analysis of
corn husk leaves. The functional groups were estimated using
Fourier Transform Infrared Spectroscopy (FTIR, Nicolet 6700,
USA). Fig 1 and 2 depict the FTIR spectrum of Corn Husk
leaves before and after adsorption of phenol and cyanide.
From Fig.1 it can be seen that there is a strong vibrational
peak at 3437.24 cm-1 which showed the presence of –OH or –
NH functional groups. The peak at 2357.19 cm-1 corresponds
to –CH stretching and the next peak at 1638.88 cm-1 between
1650-1550 cm-1 showing the presence of secondary amines.
From Fig. 2 it can be seen that after adsorption there is a
shifting of peak from 3437.24 cm -1to 3430.89 cm-1 in the
primary aliphatic alcohol (OH) region which shows the
adsorption of phenol on Corn husk leaves. Further the next
prominent shifting of peak at 2357 cm -1 to 2358.63 cm-1
shows the –CH stretching due to carbonate structures,
carboxylic groups and conjugate hydrocarbons again
indicating the adsorption of phenol. There is also a visible
shifting of peak in amine region i.e. from 1638.88 cm-1 to
1642.92 cm -1 which indicates the adsorption of –CN, as a
secondary amine group.
Fig-1: FTIR Spectra of Corn Husk Leaves before adsorption
Fig-2: FTIR Spectra of phenol and cyanide loaded Corn Husk leaves
420.21
553.56
1048.77
1242.91
1380.17
1638.88
1737.72
2357.19
2922.18
3437.24
0.15
0.16
0.17
0.18
0.19
0.20
0.21
0.22
0.23
0.24
0.25
0.26
0.27
0.28
0.29
0.30
0.31
0.32
0.33
Absorbance
5001000150020002500300035004000
Wavenumbers (cm-1)
415.05
476.69
661.84
901.46
1047.62
1241.14
1378.72
1427.63
1515.12
1642.96
1742.46
2358.63
2856.71
2922.07
3430.89
3741.23
0.000
0.005
0.010
0.015
0.020
0.025
0.030
0.035
0.040
0.045
0.050
0.055
0.060
0.065
0.070
0.075
0.080
0.085
0.090
Absorbance
5001000150020002500300035004000
Wavenumbers (cm-1)

_________________________________________________________________________________________
Further SEM analysis was also done of the adsorbent and
immobilized bacteria before and after simultaneous adsorption
and biodegradation (SAB) are shown below in Fig. 3.
(a) (b)
Fig-3: SEM images of bacteria immobilized on Corn Husk leaves (a) before SAB (b) after SAB
2.2. Batch Experiments
Batch experiments were carried out in 250 mL flat bottom
flask. These flasks were kept at an rpm of 125 in an incubator
cum orbital shaker (Metrex MO-250, India). The phenol:
cyanide ratio is taken as 10:1 as is discharged from coke waste
water (Agarwal et. al. 2013). Phenol is highly photo sensitive
so the incubator was covered with black cardboard properly
throughout the experiment. 400 mg/L phenol and 40 mg/L
cyanide were taken as initial adsorbate concentrations.
Optimum operating parameter study was carried out in the pH
range of 6-10, at a temperature of 300C and in an adsorbate
dose range of 2-10 g/L. All the experiments were carried out
for 54 h and optimum value of operating parameter was
obtained at maximum removal keeping in view both the
compounds.The initial pH of the solution was maintained after
every 2 h with 1N NaOH or HCl.For equilibrium studies, the
initial concentrations of phenol and cyanide were taken in the
range between 100-1000 mg/L and 10-100 mg/L respectively.
For kinetic study the sample was withdrawn after 6 h and then
was filtered with standard Whatman filter paper Cat No. 1001
125. The filtrate was then analysed for phenol and cyanide
using colorimetric method, 4-aminoantipyrene and picric acid
method respectively. The amount of phenol and cyanide
adsorbed per unit mass of the adsorbent was evaluated by the
following mass balance equation:
q =
C0 − Ce V
M (1)
Where C0 = initial concentration (mg/L)
Ce= Concentration at equilibrium (mg/L)
V= Volume of the solution (L)
M= Mass of adsorbent (g)
2.3 Equilibrim Isotherms
Interactive behaviour of adsorbates and adsorbents are
described by equilibrium models therefore description of
equilibrium models is necessary. Using these models the effect
that one component has on the adsorption of the other
component and their comparative affinity for binding sites can
also be studied [10]. The simple equilibrium models used for
typical adsorption processes are Langmuir model, Freundlich
model, Toth model, Redlich-Peterson model, Radke-Prausnitz
model etc. Keeping in view the present study which is based
on the simultaneous removal of pollutants from multi-
component system of phenol and cyanide multicomponent
isotherm models are used.In multicomponent systems
components interference and compete for active sites which
leads to a more complex mathematical formulation of the
equilibrium therefore single component models are not
capable of fully solving the purpose [10].These complex
multi-component systems can be modelled using variants of
single isotherm models discussed below from Eq. (4)-(8):
Non-modified competitive Langmuir:
qe,i = (Q0,ibiCe,i)/(1 + bj
N
j=1 Ce,j) (4)
Modified competitive Langmuir:
qe,i = (Q0,ibiCe,i/ni)/(1 + bj(Ce,j/nj)N
j=1 ) (5)

_________________________________________________________________________________________
Extended Langmuir:
qe,i = (Q0,ibiCe,i)/(1 + bjCe,j
N
j=1 ) (6)
Extended Freundlich:
qe,i = (KF,iCe,i
1
(n i +xi)
)/(Ce,i
xi
+ yiCe,j
zi
) (7)
qe,j = (KF,jCe,j
1
nj+xj
)/(Ce,j
xj
+ yjCe,i
zj
) (8)
2.4 Kinetic Studies
The mechanism of adsorption i.e. physisorption or
chemisorption along with the time profile and rate constant of
the adsorption kinetic are estimated by kinetic studies.
Different models used are pseudo first order (physisorption),
pseudo second order (chemisorption) Weber and Morris or
intraparticle model for mass transfer effects. Equations
describing the aforementioned models are given below from
Eq. (9)-(11):
Pseudo-first order:
qt = qe(1 − exp −k1t ) (9)
Pseudo-second order:
qt = k2qe
2
t/(1 + qek2t) (10)
Intraparticle:
qt = kid t
1
2 (11)
2.5 Model Validation
The error function, namely, Average Relative Error (ARE)
was used for validation of kinetic models as well as for
equilibrium isotherms. For ARE evaluation, equation given is:
ARE % = 100 N × (
qe,i
exp
−qe,i
cal
qe,i
exp )2
2
(12)
3. RESULTS AND DISCUSSION
3.1 Effect of pH
The effect of pH was studied in the range of 6-10. The
microbe used in the process i.e. bacteria of Serratia Sp. ceased
to grow in extreme acidic and extreme alkaline conditions.
Fig.4 shows the change in percentage removal of phenol and
cyanide with pH
.The percentage removal of phenol shows a
decrease after the pH 7 and shows a maximum removal of 76
% at a pH
between 6 and 7. This shows that phenol adsorption
takes place mainly in its undissociated form as phenol has a
pKa of 9.96 under which it remains in undissociated form. In
case of cyanide the removal percentage shows a maximum of
96 % at pH 7 and then decreases in alkaline conditions. Since
the pH is not reduced below 6, the pressure is maintained and
there is no evolution of HCN [11]. Since the pKaof cyanide is
9.39 therefore cyanide also shows the behaviour of getting
adsorbed in its undissociated form.
Fig-4: Effect of pH on removal of phenol and cyanide by SAB
3.2 Effect of Adsorbent Dose
Adsorbent dose effect was studied on the co-adsorptive
removal of phenol and cyanide between the doseof 2-10 g/L.
From the Fig.5shows that the percentage removal for both
phenol and cyanide increases with adsorbent dose till 6 g/L
and then it becomes constant. The initial increase in
percentage removal with increase in adsorbent dose is due to
the increase in active sites. However above certain dose
removal percentage assumes an asymptotic value. With
increase in adsorbent dose there can be an overlapping of
active sites which decreases the surface area on the adsorbent.
Optimum removal of 76 % phenol and 85 % cyanide occurs at
6 g/L therefore it is taken as optimum adsorbent dose.
Fig-5: Effect of adsorbent dose on the SAB process of phenol
and cyanide
10
20
30
40
50
60
70
80
90
100
4 5 6 7 8 9 10 11
%Removal
pH
Phenol
cyanide
20
40
60
80
100
120
0 1 2 3 4 5 6 7 8 9 10 11
%Removal
Adsorbent dose (g/L)
phenol
cyanide

_________________________________________________________________________________________
3.3 Effect of Initial Concentration
Driving force to overcome mass transfer limitations between
sorbate and sorbent is provided by initial adsorbate
concentration. In the case of phenol, fig 6(a) a maximum
percentage removal of about 97 % takes place at a
concentration of 100 mg/l which further decreases by
increasing the initial concentration from 200-1000 mg/L.
Similarly fig 6 (b) shows cyanide removal around 90 % at a
concentration of 10 mg/l which decreases further with
increasing concentration till 100 mg/l. At low concentrations
the active sites are easily occupied by sorbent molecules
which show a high percentage removal while at a high
concentration saturation of binding capacity of adsorbents of
adsorbent can take place which decreases removal [12].
(a) (b)
Fig-6: Effect of initial concentration of (a) phenol and (b) cyanide on the SAB process
3.4 Effect of Contact Time
Contact time study is essential for the adsorption study as it is
an important parameter for determination of equilibrium time
of adsorption process. From fig. 7 it is clearly seen thatfor
phenol an increase in removal is witnessed till 30 h where it
shows the maximum removal of 73.36 % and after that it
becomes constant. Similarly for cyanide the study revealed
that cyanide showed a trend of increasing removal with time
and reached a maximum till50 h. For both phenol and cyanide
the initial removal takes place by simple adsorption and then
the further increase in removal is adhered to the fact the
occupied sites are freed due to biodegradation [7].
Fig-7: Effect of Contact time on the removal of phenol and
cyanide by SAB process
3.5 Equilibrium Modelling:
The simultaneous adsorption and biodegradation equilibrium
data for phenol and cyanide on corn husk leaves was analysed
using Solver function of Microsoft excel 2010. The data for
multicomponent adsorption of phenol and cyanide onto corn
husk leaves were fitted to different multicomponent isotherm
models i.e. Non-modified Langmuir, Modified Langmuir,
Extended Langmuir and Extended Freundlich. These
multicomponent models use the constants from single
component models. The predictability of these models were
analysed using Average Relative Error (ARE). The data of
different isotherm models is shown in table 1. From table 1 it
can be seen that Non-modified Langmuir isotherm shows best
the simultaneous adsorption and biodegradation of phenol
with an ARE value of 9.597. Whereas Modified Langmuir
Isotherm shows best the simultaneous adsorption and
biodegradation of cyanide with an ARE value of 20.79.
0
20
40
60
80
100
120
0 200 400 600 800
%Removal
Initial Concentration (mg/L)
Phenol
0
20
40
60
80
100
0 20 40 60 80
%Removal Initial Concentration (mg/L)
Cyanide
0
20
40
60
80
100
0 10 20 30 40 50 60
%Removal
Time (h)
Phenol
Cyanide

_________________________________________________________________________________________
Table-1: Study of multi-component isotherms for the SAB process of phenol and cyanide
Parameters and ARE Present Study
Non-modified Langmuir Isotherm
Phenol (i=1) Cyanide (i=2)
Q0,i 45.172 7.393
bi 0.216 0.255
ARE 9.597 32.353
Modified Langmuir Isotherm
Q0,i 45.172 7.393
bi 0.216 0.255
ni 2.595 0.522
ARE 19.028 20.79
Extended Langmuir Isotherm
Q0,i 99.646 2.624
bi 2.186 0.255
ARE 11.317 27.197
Extended Freundlich Isotherm
KF,i 12.213 1.709
ni 3.477 2.178
xi -2.564 -3.545
yi 1.748 0.391
zi 1.231 0.958
ARE 15.357 37.716
Fig-8: Equilibrium isotherms for phenol at 300C at 400 mg/L
concentration Fig-9: Equilibrium isotherms for cyanide at 300C at 40 mg/L
concentration
From fig 8.and fig 9. It can again be seen that the closest to
phenol experimental data is given by non-modified Langmuir
adsorption isotherm and for cyanide the closest fit is given by
modified adsorption isotherm.
0
10
20
30
40
50
60
70
0 200 400 600 800
SpecificUptake(mg/g)
Initial Phenol Concentration (mg/L)
Experimental
Non modified
Langmuir
0
1
2
3
4
5
6
7
0 20 40 60 80
SpecificUptake(mg/g)
Initial Cyanide Concentration (mg/L)
Experimental
Non modified Langmuir
Modified Langmuir
Extended Langmuir

_________________________________________________________________________________________
3.6 Kinetic Studies
Estimation of adsorption mechanism i.e.physisorption
(pseudo-first order) or chemisorption (pseudo- second order)
can be determined by kinetic modelling. From table 2 given
below the inferences drawn are as follows: kinetic data
prediction of phenol is better shown by pseudo-first order
model as it has a lower ARE but since there is not much
difference in the ARE for both the models it can be said that
phenol adsorption takes place both by physisorptionand
chemisorption whereas for cyanide kinetic data can be better
predicted by pseudo second order kinetics attributing to the
fact of lower ARE but due to slight difference in ARE values
for pseudo first order and second order kinetics cyanide
adsorption kinetics can also be predicted by both first and
second order kinetics. Hence for both phenol and cyanide
adsorption takes place both by physisorption and
chemisorption. Diffusion nature is determined by graph of qtvs
t0.5
.The graph of qtvs t0.5
was plotted for both phenol and
cyanide. According to [6] the plot should be linear for the
involvement of intraparticle diffusion. Since the obtained plot
fig. is non-linear and it does not pass through origin,
intraparticle diffusion is not the rate controlling step and other
kinetic models control the rate of adsorption [3,8].For phenol
(R1
2
>R2
2
) which indicates surface diffusion to be dominating
whereas for cyanide (R2
2
>R1
1
) which shows that intraparticle
diffusion as the dominating step [2].
Table-2: Kinetic data estimation for SAB process of phenol and cyanide
Parameters and ARE Present Study
Pseudo First Order Kinetics
Phenol Cyanide
qe,cal 66.445 10.278
k1 0.034 0.016
ARE 4.043 4.003
Pseudo Second Order Kinetics
qe,cal 104.548 17.502
k2 0.000215 0.000548
ARE 4.557 3.992
Intraparticle
kid 1 11.862 1.013
R1
2
0.9805 0.9703
kid 2 0.657 0.0428
R2
2
0.9182 1
Fig-10: Comparative plots for experimental and calculated
values of qt by pseudo first order and pseudo second order
kinetics for phenol at 300
C and 400 mg/L concentration
Fig-11:Comparativeplots for experimental and calculated
values of qt by pseudo first order and pseudo second order
kinetics for cyanide at 300C and 40 mg/L concentration
0
10
20
30
40
50
60
70
0 20 40 60
qt(mg/g)
Time (h)
Experimental
Pseudo first order
Pseudo Second order
0
1
2
3
4
5
6
7
0 20 40 60
qt(mg/g)
Time (h)
Experimental
Pseudo first order
Pseudo second order

_________________________________________________________________________________________
Fig-12: Intraparticle plots for phenol
Fig-13: Intraparticle plots for cyanide
CONCLUSIONS
Present study is based on removal of phenol and cyanide by
simultaneous adsorption and biodegradation. The biosorbent
used in this process is Corn Husk leaves and the microbe used
is the bacteria of Serratia Sp. The initial concentration for
phenol and cyanide was taken as 400 mg/L and 40 mg/L
respectively and the SAB experiments were performed for 60
h at 300
C. The optimum pH was between 6-7 and the
optimum adsorbent dose was estimated as 6 g/L. The removal
of phenol and cyanide were 75 % and 83 % respectively.
Equilibrium isotherms plotted showed that SAB of phenol was
best estimated by non- modified Langmuir isotherm and SAB
of cyanide was best estimated by modified Langmuir
isotherm. Kinetic studies revealed that SAB process of both
phenol and cyanide takes place by both physisorption and
chemisorption and that for Phenol surface diffusion is
dominating and for cyanide intraparticle is dominant but since
the intraparticle plots do not pass through origin which shows
that intraparticle diffusion is not the rate controlling step.
ACKNOWLEDGEMENTS
The authors are thankful to Ministry of Human Resource
Development, Government of India and Institute’s
Instrumentation Center, IIT Roorkee for extending their
financial and technical support for present research work.
REFERENCES
[1] Z. Aksu, F. Gonen, Biosorption of phenol by
immobilized activated sludge in a continuous packed
bed: prediction of breakthrough curves, Process
Biochemistry 39 (2004) 599–613.
[2] B. Agarwal ,C.B. Majumder, P.K. Thakur,
Simultaneous co-adsorptive removal of phenol and
cyanide from binary solution using granular activated
carbon, Chem. Eng. J. 228 (2013) 655–664.
[3] G. Moussavi, R. Khosravi, Removal of cyanide from
wastewater by adsorption onto pistachio hull wastes:
Parametric experiments, kinetics and equilibrium
analysis, J. of Hazard. Mater. 183 (2010) 724–730.
[4] CERCLA, The Priority List of Hazardous Substances,
Substance Priority List (SPL), from the Comprehensive
Environmental Response, Compensation, and Liability
Act (CERCLA) section 104 (i), as amended by the
Superfund Amendments and Reauthorization Act
(SARA).
[5] R. R. Dash, A. Gaur, C.Balomajumder, Cyanide in
industrial wastewaters and its removal: A review on
biotreatment, J. Hazard. Mater. 163 (2009) 1–11.
[6] M. Kilic, E. Apaydin-Varol, A. E. Putun, Adsorptive
removal of phenol from aqueous solutions on activated
carbon prepared from tobacco residues: Equilibrium,
kinetics and thermodynamics, J. Hazard. Mater. 189
(2011) 397–403.
[7] B. Agarwal ,C. Balomajumdar, Simultaneous
Adsorption and Biodegradation ofPhenol and Cyanide
in Multicomponent System, Inter. J. Environ. Eng.
Manage.ISSN 2231-1319, Volume 4, Number 3 (2013),
pp. 233-238
[8] R.R. Dash, C. Balomajumder, A. Kumar, Treatment of
cyanide bearing water/wastewater by plain and
biological activated carbon, Ind. Eng. Chem. Res. 48(7)
(2009) 3619–3627.
[9] G. Moussavi, S. Talebi, Comparing the efficacy of a
novel waste-based adsorbentwith PAC for the
simultaneous removal of chromium (VI) and cyanide
from electroplating wastewater, Chem.Eng.Res.Des.90
(2012) 960-966.
[10] B.Agarwal, P.Sengupta, C.Balomajumder, Equilibrium,
Kinetic and Thermodynamic Studiesof Simultaneous
Co-Adsorptive Removal of Phenoland Cyanide Using
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No:11, 2013.
[11] M.D. Adams, Removal of cyanide from solution using
activated carbon, Minerals Eng.7 (1994) 1165-1177.
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Adsorptive Removal of Cyanide and Phenol
fromIndustrial Wastewater: Optimization of Process
Parameters, Res .J. Chem. Sci. Vol. 1(4) 30-39 (2011).
y = 11.86x - 18.10
R² = 0.980
y = 0.657x + 46.39
R² = 0.918
0
10
20
30
40
50
60
0 1 2 3 4 5 6 7 8
qt
Square root time h0.5
y = 1.013x - 1.571
R² = 0.973
y = 0.042x + 5.479
R² = 1
0
1
2
3
4
5
6
7
0 2 4 6 8
qt
Square root time h0.5

Potential of corn husk leaves for the co removal of phenol and cyanide from waste water using simultaneous adsorption and biodegradation

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