J. Nig. Soc. Phys. Sci. 3 (2021) 414–422

Journal of the
Nigerian Society

of Physical
Sciences

Waste glass: An excellent adsorbent for crystal violet dye, Pb2+
and Cd2+ heavy metal ions decontamination from wastewater

K. O. Sodeinde∗, S. O. Olusanya, D. U. Momodu, V. F. Enogheghase, O. S. Lawal

Materials and Nanoresearch Unit, Department of Industrial Chemistry, Federal University Oye-Ekiti, Ekiti State, Nigeria.

Abstract

The suitability of waste glass as an eco-friendly adsorbent for the removal of crystal violet (CV) dye, Pb2+ and Cd2+ heavy metal ions in waste
water samples was investigated in batch mode. Waste glass sample was pulverized and characterized by SEM/EDX, XRD, BET and FTIR. Effects
of variation in temperature, pH, contact time and recyclability of the adsorbent were studied. FTIR spectra revealed major peaks around 491.53
and 3444.12 cm−1 corresponding to the bending vibrations of Si-O-Si and -OH groups respectively. SEM/EDX analysis showed a dense, coarse,
porous morphology with predominantly silica component. The effective surface area and size of the adsorbent were 557.912 m2/g and 2.099 nm
respectively. Increase in temperature, dosage, contact time resulted in increase in adsorption efficiency. Optimum adsorption efficiency of 94%,
97.5% and 89.1% was attained for Pb2+, Cd2+ ions and CV dye respectively at 70◦C. Adsorption process followed more accurately pseudo-first
order model and isotherm fitted perfectly into Freundlich model indicating a multilayer adsorption mechanism for CV dye and the heavy metals.
89.87% reduction in Chemical Oxygen Demand (COD) level of wastewater was reported upon treatment with waste glass adsorbent affirming its
efficiency for dye and heavy metal pollutants removal.

DOI:10.46481/jnsps.2021.261

Keywords: waste glass, crystal violet dye, heavy metals, adsorption, wastewater

Article History :
Received: 18 June 2021
Received in revised form: 26 September 2021
Accepted for publication: 27 September 2021
Published: 29 November 2021

c©2021 Journal of the Nigerian Society of Physical Sciences. All rights reserved.
Communicated by: E. Etim

1. Introduction

Glass is one of the earliest man-made materials. It is an in-
organic, non-crystalline material obtained by melting, homog-
enization, cooling and finishing of components such as sand,
sodium oxide, limestone, etc. Glass has found useful appli-
cations in television screens, glass bottles, doors, car wind-
screens, packaging materials, certain industrial and scientific
equipment, etc, [1]. Increasing global population and industri-
alization have led to a sharp rise in the use of glass products in

∗Corresponding author tel. no: +2348147773137
Email address: kehinde.sodeinde@fuoye.edu.ng (K. O. Sodeinde )

household and industrial devices resulting in the generation of
huge volume of waste glass. According to the United Nations
estimates, the annual global amount of disposed solid waste is
said to be 200 million tons, comprising 7% glass [2]. Generally,
glass is relatively stable, non-biodegradable, resistant to attack
and outdoor temperature [3]. Recycling is a useful method of
reducing pollution load associated with waste glass. However,
poor financial and technological capacity for proper waste glass
recycling remain a major problem particularly in developing
countries.

Although dyes have numerous applications in food, cosmet-

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K. O. Sodeinde et al. / J. Nig. Soc. Phys. Sci. 3 (2021) 414–422 415

ics, pharmaceutical and textile industries, improper discharge
of effluents containing dyes into water bodies negatively impact
on their aesthetic value; threaten the survival of aquatic species
by impairing photosynthesis, etc, [3, 4]. Bioaccumulation of
dyes and heavy metals especially lead and cadmium in living
cells can lead to impairment of haemoglobin synthesis, neuro-
logical disorder, kidney damage, carcinogenicity, mutagenicity,
etc. [5]. In particular, exposure of pregnant women to elevated
levels of lead may result in miscarriage, stillbirth, premature
birth, deformities, etc, [6]. Several methods such as adsorption,
ion exchange, photo-degradation, physical precipitation, etc,
have been reported for the removal of dyes and heavy metals in
the environment [7, 8, 9, 10, 11]. Of these methods, adsorption
remains the most attractive based on cost, ease of operation,
analysis time, etc [12]. Different natural and synthetic materi-
als including clay, activated carbon, termite mounds, agricul-
tural wastes (sawdust, brans, banana peels), etc. have been in-
vestigated as economic adsorbents for decontamination of dyes
and heavy metals [13, 14, 15, 16]. For instance, Ahmad re-
ported the removal of crystal violet (CV) dye by adsorption us-
ing coniferous pinus bark powder [17]. The amount of CV dye
uptake increased with increase in initial pH, dye concentration
and contact time but decreased with adsorbent dosage increase.
Equilibrium was attained in 2 h. The isotherm fitted most into
Langmuir model indicating a monolayer adsorption mechanism
while the kinetics followed perfectly a pseudo second order rate
equation. Also, fly ash and rice husk adsorbents were investi-
gated for the removal of copper, lead, cadmium, nickel and iron
heavy metals [18]. The rice husk adsorbent showed better affin-
ity towards iron, nickel and lead while fly ash was more effec-
tive for the removal of copper and cadmium [18].

Crystal violet (CV) is categorized under the triarylmethane
dyes. It is equally referred to as hexamethyl pararosaniline
chloride, gentian violet, etc [9]. It possesses antibacterial, an-
tifungal and antihelminthic properties [7]. It is widely used as
a histological stain, for paints and textile applications [19]. CV
dye is carcinogenic, non-biodegradable, persistent in the envi-
ronment due to its poor metabolism by microorganisms [11].
Access to clean water and environmental sanitation remains a
key objective of the Sustainable Development Goals (SDGs) of
the United Nations (UN). Utilisation of waste glass as a cheap
and effective adsorbent for the decontamination of toxicants
in polluted water bodies would promote cleaner environment,
minimise water pollution and improve quality of life especially
in rural communities of developing nations. Thus, the focus of
the work was to utilise waste glass from the local environment
for the decontamination of crystal violet (CV) dye and toxic
heavy metal ions (Pb2+ and Cd2+ ions) in aqueous medium.
Effects of variations in pH, temperature, adsorbent dosage, pol-
lutant concentration, recyclability on the adsorption efficiency,
kinetics, adsorption isotherm and practical application in the
treatment of waste water are herein presented.

2. Methodology

2.1. Materials/Reagents
All the chemicals used were of analytical reagent grade or

the highest purity available.

2.2. Sample collection and treatment
2.0 kg of transparent soda-lime wasteglass bottle samples

were collected around Oye town, Ekiti state, Nigeria. The sam-
ples were cleaned and ground into fine powder by dry ball milling
machine operated at ambient temperature for 8 h. The pul-
verised wasteglass (particle size 75 µm) was carefully kept in
a glass vial and stored at room temperature (30 ± 2◦C) till fur-
ther use.

2.3. Scanning electron microscopy/Energydispersive X-ray (SEM/EDX)
analysis

Morphological features and surface characteristics of glass
sample were obtained from scanning electron microscopy/Energy
Dispersive X-ray (SEM/EDX) using a JEOL USA Model: JSM-
7900F. A thin layer of waste glass sample granule was placed
on aluminium specimen holder by double-sided tape. The spec-
imen holder was loaded in a polaron SC 7610 sputter coater
and coated with gold to a thickness of about 30nm to prevent
charging. The specimen holder was transferred to XL-20 series.
SEM/EDX analysis was conducted at an accelerating voltage
of15-20 kV.

2.4. Fourier transform infra red (FTIR) spectroscopic analysis
FTIR spectra of the waste glass samples were run as KBr

pellets on Perkin Elmer Spectrum Two TM spectrometer in the
frequency range 4000 − 400 cm−1.

2.5. X-ray Diffraction studies
X-ray diffraction patterns of powdered waste glass sample

was obtained using Empyrean XRD diffractometer at 40 mA
and 45 kV with Cu Kα (1.5418 Å) radiation at an angular inci-
dence of 10 − 75◦.

2.6. Brunauer-Emmett-Teller (BET) surface area analysis
The specific surface area (BET) of powdered waste glass

sample was measured with a Quantachrome surface analyzer
using N2 as the standard adsorbate. Prior to analysis, the sample
was degassed at 523 K for 3 h. The pore size and pore volume
were estimated using Barrett-Joyner-Halenda (BHJ) theory.

2.7. Batch adsorption experiment
Batch adsorption method as reported by Ayanda et al. [20]

was adopted with slight modification. Briefly, a range of pow-
dered waste glass (0.1 g - 1.0 g) was contacted with 40 mL of
5 mg/L CV dye and stirred at 300 rpm at 40◦C for 30 min for
the effect of waste glass adsorbent dosage. To investigate the
influence of pH on the adsorption process, the pH of 40 mL of
5 ppm CV dye solution containing 0.5 g waste glass adsorbent
was adjusted to pH range 2-10 using either 0.1 M HCl or 0.1
M NaOH. The effect of time was studied between 20-60 min

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K. O. Sodeinde et al. / J. Nig. Soc. Phys. Sci. 3 (2021) 414–422 416

while the effect of temperature was determined at a tempera-
ture range of 30-70 oC. On the effect of initial dye concentra-
tion, 40 mL of 1, 5, 10, 15 and 20 ppm CV dye were used along
with 0.5 g powdered waste glass adsorbent at 40◦C for 30 min.
The resulting mixture after each experiment was filtered and
absorbance of the aliquot of the filtrate was determined using
T-60 UV-Visible spectrophotometer at 592 nm. For the Pb2+

and Cd2+ heavy metal ions determination, the same procedure
was repeated. The Pb2+ and Cd2+ levels were analysed using
Atomic Absorption Spectrophotometer (AAS Buck Scientific
model 211 VGP) with the respective hollow cathode lamps. The
adsorption efficiency experiments were carried out for three re-
peated cycles to study the recyclability and stability of the waste
glass sorbent. After each cycle, the adsorbent was filtered and
oven-dried at 70◦C before reuse for the next cycle. For practical
application of the adsorption efficiency of the waste glass sor-
bent, effluent from local textile (Adire) industry was collected
in a glass bottle and analysed before and after treatment (0.5 g
waste glass contacted with 40 mL effluent at 300 rpm, pH 6,
40 oC for 30 min) for the levels of Pb2+, Cd2+ ions and CV
dye. The chemical oxygen demand (COD) was equally deter-
mined before and after treatment using standard method [21].
Duplicate analysis was conducted for all blank solutions, stan-
dards and samples. The percentage CV dye and heavy metal
ions (Pb2+ and Cd2+) adsorption efficiency was obtained using:

% adsorption efficiency = C0 − Ce/C0 × 100, (1)

where C0 is the initial concentration of analyte (CV dye/heavy
metal) and Ce is the equilibrium concentration of analyte. The
equilibrium adsorption capacity (mg of analyte per g waste glass)
was calculated using:

qe = C0 − Ce/W × V, (2)

where C0 and Ce (mg/L) are the initial and equilibrium con-
centrations of the CV dye/heavy metal solution. V (mL) is the
volume of the solution, W (g) is the mass of waste glass used
and qe (mg/g) is the amount adsorbed.

2.8. Adsorption isotherm

In this study, the adsorption isotherms described by Lang-
muir and Freundlich were used. The Langmuir isotherm is
based on the theoretical principle that the adsorption sites are
of equal energy and the coverage of adsorbate molecules on a
solid surface occurs only in a monolayer. The linearised form
of the Langmuir model is given by

1
qe

=
1

qm KL
×

1
Ce

+
1

qm
, (3)

where Ce is the equilibrium concentration of pollutant analyte
solution (mg/L), qe is the concentration of pollutant adsorbed
per unit mass of the waste glass (mg/g), qm is the Langmuir con-
stant denoting adsorption capacity (mg/g), and KL is Langmuir
constant denoting energy of adsorption (L/mg). A linear plot of
1/qe against 1/Ce is the underlying basis of this equation with
KL and qm determined from the slope and intercept respectively.

The linear form of the Freundlich equation is written as:

log qe = log KF + 1/n log Ce, (4)

where Ce is the equilibrium concentration of pollutant analyte
solution (mg/L), qe is the concentration of pollutant adsorbed
per unit mass of the waste glass (mg/g) while n is the number
of layers and KF is the Freundlich constant. KF and n values
are deduced from the respective intercept and slope of the linear
plot of log qe against log Ce.

2.9. Kinetic models studies

For detailed studies of the adsorption kinetics of Pb2+, Cd2+

ions and CV dye on the waste glass sample, the Lagergren
pseudo-first-order model [22] and pseudo-second-order kinetic
model [23] were used. They are given, respectively, as:

ln(qe − qt) = ln qe − k1t, (5)

t/qt = 1/(k2 · q
2
e ) + t/qe, (6)

where qt and qe are the amount of pollutant adsorbed (mg/g) at
time t and equilibrium, respectively. k1 (min−1) is the rate con-
stant of the pseudo-first-order kinetic model and k2 (g · mg−1·
min−1) is the rate constant of the pseudo-second-order kinetic
model.

3. Result and Discussion

3.1. SEM/EDX and BET surface area analyses of waste glass
powder

Surface morphology and chemical composition of an ad-
sorbent play a major role in ascertaining the efficiency and ef-
fectiveness of the adsorption process. The SEM image (Figure
1a) of the porous waste glass showed a dense, coarse, porous
surface morphology. EDX analysis (Figure 1b) revealed the %
composition of the waste glass in the following order:
Si>Mg>C>O>Ca>Fe>S>Na>K. These elements are present
in form of oxides (e.g. SiO2, MgO, Fe2O3, etc.), carbonates
(calcium carbonate, sodium carbonate, potassium carbonate,
etc), silicates; with silica as the predominant component. The
BET specific surface area of the waste glass was about 557.912
m2/g while the Barrett, Joyner, Halenda (BJH) surface area was
measured to be about 663.9 m2/g. The BJH pore volume was
calculated to be about 0.3264 cc/g with an average pore size
of 2.099 nm (see Figure 2).The dense, coarse, porous nature of
the glass surface coupled with interaction with various chemi-
cal components facilitated adsorption of pollutant analytes onto
its surface under prevailing conditions.

3.2. FTIR spectra of waste glass

The result of the FTIR analysis of the porous waste glass
particles is shown in Figure 3. The peaks at 412.31, 419.22,
431.95, 444.07, 451.09, 455.22, 473.95, 482.59 and 491.53
cm−1 revealed bending vibrations of Si–O–Si, while the peaks
at 528.01, 519.90, 504.54, 511.85 cm−1 showed the stretching
vibration of O–Si–O. The peaks observed at 605.00, 645.43,

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K. O. Sodeinde et al. / J. Nig. Soc. Phys. Sci. 3 (2021) 414–422 417

(a) (b)

Figure 1: (a) SEM image (b) EDX analysis of waste glass powder

Figure 2: BET surface area plot of waste glass

644 and 694.53 cm−1 correspond to stretching vibrations of Si–
O–Al and M–X [3]. The peaks at 3444.12, 3563.40, 3605.19
and 3838.03 cm−1 indicate the –OH group from the silanol (Si–
OH) or adsorbed water molecule trapped within the silicate
structure of the waste glass particles [24]. In general, the vari-
ous peaks in the spectra confirmed the presence of silicates, car-
bon, metal oxides, and metal halides in the waste glass particles
[3]. These functional groups played crucial role in the overall
adsorption of analytes at the sorbent surface through electro-
static interaction, precipitation, etc.

3.3. XRD pattern of waste glass

XRD pattern of the waste glass powder is shown in Figure
4. The prominent peak at 2θ = 27.1◦ corresponds to the silica-
silica bond. Smaller peaks at 2θ = 22.5◦, 29.5◦, 35.2◦, 37.3◦,
40.4◦, 44.3◦, 51.5◦, 60.2◦, and 68.3◦ are due to the presence
of other mineral components including sodium oxide, calcium
oxide, etc in the waste glass [3]. This result agreed with other
previous studies on waste glass [25].

Figure 3: FTIR spectra of waste glass powder

Figure 4: XRD pattern of waste glass powder.

3.4. Result of adsorption studies

3.4.1. Effect of temperature
The effect of temperature on the adsorption efficiency is pre-

sented in Figure 5a. Increasing the temperature of the medium
from 30 − 70◦C resulted in increase in the % adsorption effi-
ciency of analytes (CV dye, Pb2+ and Cd2+ metal ions). Max-
imum % adsorption efficiency was attained at 70◦C in all the

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K. O. Sodeinde et al. / J. Nig. Soc. Phys. Sci. 3 (2021) 414–422 418

analytes. This might be due to the increase in the average ki-
netic energy, collision frequency and higher diffusion rate of
the analytes to the porous glass powder surface at higher tem-
perature. Aniagor and Menkiti [7] reported similar observation
at elevated temperature using lignified bamboo isolate for the
removal of crystal violet dye effluent.

3.4.2. Effect of pH
The degree of acidity or alkalinity of the medium plays cru-

cial role in the overall adsorption process by facilitating precip-
itation, co-precipitation and sorption processes through electro-
static interaction (attraction or repulsion) of charges between
the adsorbent and adsorbate at the surface. For this study, the
effect of pH was studied between pH 2-10 at 40◦C, 0.5 g ad-
sorbent dosage for 30 min. In the case of CV dye, a reduc-
tion in % adsorption efficiency was observed as the pH pro-
gressed from 2-10 (Figure 5b). The silicate glass surface (ad-
sorbent) acquired a negative surface charge density in aqueous
medium largely due to the dissociation of the silanol (Si–OH)
group. The observed decrease in % adsorption efficiency might
be due to an increase in electrostatic repulsion between the neg-
atively charged –OH group of the silanol (in the adsorbent) and
the –OH group of the aqueous medium of equal ionic size and
charge at higher pH. These negatively charged –OH ions thus
occupy position far away as possible from the adsorbent surface
to minimize electrostatic repulsion. Consequently, less neg-
atively charged species are available at the adsorbent surface
for adsorption (via electrostatic attraction with the cationic CV
dye) and hence the reduction in % adsorption efficiency. Unlike
the case of CV dye, increasing the pH of the medium resulted in
gradual increase in the adsorption efficiency of the heavy met-
als (Pb2+ and Cd2+). At higher pH (alkaline medium), pre-
cipitation of Pb2+ and Cd2+ ions readily occur on the glass
(adsorbent) surface thus favouring higher adsorption efficiency.
This implied that the energy barrier required for precipitation is
much less than electrostatic repulsion between the –OH group
of the silanol (adsorbent) and the –OH group of the aqueous al-
kaline medium. The observed variation in pH of this work is in
contrast to the earlier studies on CV dye removal using treated
ginger waste [26].

3.4.3. Effect of adsorbate concentration
Adsorption experiments were carried out at a concentra-

tion range of 1-20 ppm with an adsorbent dosage of 0.5 g of
waste glass adsorbent at 30◦C for 30 min (Figure 6a). The re-
sult showed a gradual increase in the % adsorption efficiency
as the adsorbate concentration increased for the heavy metal
ions and the CV dye. This might be due to large surface area
(with sufficient active sites), retardation of resistance towards
adsorbate uptake, which increase diffusion to the surface and
relatively small adsorbent pore size for effective trapping of
adsorbate ions [9]. At 15 ppm, % maximum adsorption effi-
ciency (equilibrium) was attained for the pollutant (adsorbate)
molecules signaling the maximum saturation at the adsorbent
surface. Above 15 ppm, the adsorbent surface became supersat-
urated with the pollutant molecules hence the slight reduction
in the adsorption efficiency.

3.4.4. Effect of adsorbent dosage
The study of the adsorbent dosage effect was important in

order to ascertain the minimum possible dosage amount with
the maximum adsorption efficiency. From Figure 6b, it was
observed that the adsorption efficiency increased progressively
as a function of the waste glass dosage (0.1-1.0 g). This is due
to the fact that more porous active sites became more readily
accessible to the adsorbate ions (Pb2+, Cd2+ ions and CV dye)
for surface adsorption. Maximum % adsorption efficiency of
75%, 94% and 97.5% was recorded for CV dye, Pb2+ and Cd2+

ions, respectively.

3.4.5. Regeneration efficiency of waste glass adsorbent
The regeneration efficiency is a measure of recyclability and

stability of an adsorbent per number of consecutive adsorption
cycle. For this study, the waste glass adsorbent was investigated
for three consecutive runs for the removal of CV dye, Pb2+ and
Cd2+ ions (Figure 7). The result showed a slow, steady reduc-
tion in regeneration efficiency of the adsorbent over the three
runs in the following order: Cd2+ >CV dye > Pb2+. % regen-
eration efficiency for the first repeated cycle is 78%, 72% and
61% for Cd2+, CV dye and Pb2+ ions respectively. This reduced
to 57%, 50% and 45% for Cd2+, CV dye and Pb2+, respectively
after the third cycle. The relative stability and efficiency of the
waste glass adsorbent might be due to its relatively large pore
size, specific surface area and pore volume which facilitated
easy adsorption and separation of adsorbates at the porous glass
surface.

3.5. Adsorption isotherm and kinetic models

Figure 8 shows the plots obtained for the Langmuir and Fre-
undlich adsorption isotherm models for the pollutants; CV dye,
Pb2+ and Cd2+ ions. The slopes, intercepts and the correspond-
ing constants of the models are presented in Table 1. In all
the cases studied, the regression (R2) values are much relatively
higher for the Freundlich isotherm model than the Langmuir
isotherm model indicating that the Freundlich model is more
favoured by the adsorption process.

This implied that the uptake of CV dye and the heavy metal
analytes occurred on a heterogeneous surface by multilayer ad-
sorption and there is a non-uniform distribution of the heat of
adsorption over the porous waste glass surface. Based on the
foregoing, the separation factor (RL); a useful non-dimensional
parameter in isotherm studies was determined. RL described
the suitability of the porous waste glass powder and its affinity
towards CV dye, Pb (II) and Cd (II) ions. RL value was calcu-
lated using:

RL = 1/(1 + KLC0), (7)

where C0 is the initial concentration and KL signifies the Lang-
muir constant. Four probabilities exist for the value of RL :
RL > 1.0, RL = 1, 0 < RL < 1, and RL = 0, indicating unfa-
vorable, linear, suitable, and irreversible degrees, respectively.
From Table 1, the calculated RL values are 0.19, 0.41 and 0.33
for CV dye, Pb (II) and Cd (II) metal ions, respectively, indicat-
ing the suitability of the adsorption process using porous waste

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K. O. Sodeinde et al. / J. Nig. Soc. Phys. Sci. 3 (2021) 414–422 419

(a) (b)

Figure 5: Effect of: (a) temperature on the adsorption efficiency of waste glass (stirring speed = 300 rpm, contact time = 30 min, dosage = 0.5 g, initial concentration
= 5 ppm each of CV dye at 592 nm, Pb2+ and Cd2+), (b) pH on the adsorption efficiency of waste glass (temperature = 30◦C, stirring speed = 300 rpm, contact time
= 30 min, dosage = 0.5 g, initial concentration = 5 ppm each of CV dye at 592 nm, Pb2+ and Cd2+).

(a) (b)

Figure 6: (c) Effect of initial concentration on the adsorption efficiency of waste glass (temperature = 30◦C, stirring speed = 300 rpm, contact time = 30 min, dosage
= 0.5g). (d): Effect of dosage on the adsorption efficiency of waste glass (temperature = 30◦C, stirring speed = 300 rpm, contact time = 30 min, concentration = 5
ppm).

Table 1: Adsorption isotherms and separation factor parameters

Adsorbate Langmuir
isotherm model
constants

Freundlich
isotherm
model con-
stants

Separation factor (RL)

CV dye KL = 11.57
qm = 12.34 mg/g
R2 = 0.895

KF = 12.08
n = 3.66
R2 = 0.991

0.19

Pb2+ KL = 1.50
qm = 166.7 mg/g
R2 = 0.972

KF = 89.54
n = 1.78
R2 = 0.985

0.41

Cd2+ KL = 1.88
qm = 66.67 mg/g
R2 = 0.936

KF = 422.67
n = 0.65
R2 = 0.952

0.33

glass powder. We have also studied the kinetics of adsorption
of the three pollutants onto the surface of the waste glass us-

ing the pseudo-first and second order kinetic models (Figure 9).
The pseudo-first and -second rate constants derived from Fig-

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K. O. Sodeinde et al. / J. Nig. Soc. Phys. Sci. 3 (2021) 414–422 420

Figure 7: Regeneration efficiency of waste glass.

(a)

(b)

Figure 8: (a) Langmuir and (b) Freundlich adsorption isotherms

ure 9 are summarized in Table 2. The data in Table 2 suggested
that the rate of adsorption of the three pollutants is faster with
the first order kinetic and that the adsorption processes conform
more to the first order kinetics than the second order kinetics
(from the regression values) implying a favourable physisorp-
tion adsorption mechanism of the pollutants.

(a)

(b)

Figure 9: Pseudo-first (a) and pseudo-second (b) order kinetic plots.

Table 2: Pseudo first order and second order kinetic model parameters.

Parameter CV dye Cd (II) Pb (II)
k1(min−1) 0.0065 0.0491 0.0166

R2 0.9066 0.8688 0.9711
k2(g · mg−1min−1) 0.0007 0.0471 0.0036

R2 0.8999 0.8294 0.9525

3.6. Treatment of textile effluent
Practical application of the waste glass powder adsorbent

was investigated in the treatment of textile dye effluent. The
COD, CV dye, Pb2+ and Cd2+ ions levels of the effluent were
determined before and after treatment of the wastewater. The
COD is a measure of the amount of oxygen required for chem-
ical oxidation of organic pollutants in an effluent (e.g. textile
wastewater). The result showed a significant reduction in the
COD value from 694.26 ± 0.21 mg/L to 70.34 ± 0.08 mg/L af-
ter treatment representing 89.87% decrease in COD level thus
affirming its pollutant removal capacity. The result of this work
is comparable to previous studies on treatment of textile ef-
fluents using different adsorbents [20, 27]. Exposure to high
levels of cadmium from untreated effluent discharge had been
reported as a major cause of “itai-itai” disease; an ailment char-
acterised by kidney malfunctioning, osteomalacia, marked de-
calcification, etc [28]. Upon treatment of the textile effluent

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K. O. Sodeinde et al. / J. Nig. Soc. Phys. Sci. 3 (2021) 414–422 421

with waste glass powder adsorbent, % adsorption efficiency of
81.69%, 82.2% and 89.5% was achieved for CV dye, Pb (II)
and Cd (II) ions, respectively (Figure 10). Pb2+(0.004 ± 0.19
mg/L) and Cd2+(0.001 ± 0.14 mg/L) concentrations obtained
after treatment are relatively much lower than the 0.01 mg/L
and 0.003 mg/L World Health Organisation recommended val-
ues for Pb (II) and Cd (II) metal ions respectively in drinking
water [6].

Figure 10: Adsorption efficiency of waste glass for the removal of CV dye at
592 nm, Pb2+ and Cd2+ ions in a textile dye wastewater (effluent volume= 40
mL, stirring speed = 300 rpm, temperature = 30◦C, contact time = 30 min,
dosage = 0.5 g).

4. Conclusion

Waste glass from local environment was pulverized, charac-
terized and successfully applied for the removal of Pb2+, Cd2+

ions and CV dye in waste water. Structural crystallinity, sur-
face morphology, functional groups and surface area analyses
of the porous waste glass showed predominantly silica crys-
talline phases with highly active –OH group on the dense, coarse,
porous glass adsorbent. The pH of the medium strongly influ-
enced the adsorption process via electrostatic interaction and
precipitation. The adsorption isotherm and kinetics of the pro-
cess favoured Freundlich isotherm and pseudo-first order mod-
els, respectively. The waste glass adsorbent displayed remark-
able efficiency and effectiveness in the practical treatment of
textile effluent and can thus be recommended for the removal
of other environmental pollutants.

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