Indonesian Journal of Environmental
Management and Sustainability
e-ISSN:2598-6279 p-ISSN:2598-6260
Research Paper
Adsorption and Regeneration of Indonesian Natural Pumice for Total Chromium
Removal from Aqueous Solution
Shinta Indah1 *, Denny Helard1 , Fitria Marchelly1 , Dean Eka Putri1
1 Department of Environmental Engineering, Faculty of Engineering, University Andalas, Padang, Indonesia, Kampus Unand Limau Manis, Padang, West Sumatera, Indonesia 25163
*Corresponding author e-mail: accountname@email.com
Abstract
To investigate the potential of adsorption and regeneration of natural pumice from West Sumatera Indonesia for total chromium
(Cr) removal from aqueous solution, batch experiments in multiple adsorption-desorption cycles were performed. The results
indicated that the optimum condition of total Cr removal were 3 of pH solution, 0.3 g/L of adsorbent dose, 60 min of contact
time of adsorption, < 63 µm of diameter of adsorbent, and 1 mg/L of total Cr initial concentration with 2.226 mg Cr/g pumice
of total Cr uptake. The experimental data obtained were fitted with the Freundlich adsorption isotherm within the concentration
range studied. Desorption efficiencies for total Cr ions by using 0.1 M HCl as desorbing agent were in the range of 31-32%. Although
complete desorption were not attained, the natural pumice could be sufficiently reused up to 3 cycles of adsorption- desorption
with increasing trend in total Cr uptake that may due to the surface modification of natural pumice caused by HCl. Overall results
revealed that easy availability of natural pumice as local mineral in West Sumatra, Indonesia and its ability to adsorb and retain total
Cr will create more interest to develop new natural adsorption method of pollutant removal from solution.
Keywords
Adsorption; desorption; natural pumice; regeneration; total chromium
Received: 12 February 2018, Accepted: 16 May 2018
https://doi.org/10.26554/ijems.2018.2.2.30-27
1. INTRODUCTION
Chromium is an essential element that is required in small
amounts for carbohydrate metabolism, but becomes toxic at
higher concentrations. Chromium compounds are environmental pollutants occurring in soil, water and industrial effluents because they are widely used in many industrial activities.
In the natural environment, chromium is present in two stable
oxidation states, Cr(III) and Cr(VI), where the ratio of the two
compounds varies depending on pH value, redox potentials, total chromium concentration and redox reaction kinetics. Cr(VI)
is highly toxic, mutagenic, carcinogenic and teratogenic. Cr(III)
is much less toxic and mutagenic than Cr(VI), but long-term
exposure to high Cr(III) concentrations may cause allergic skin
reactions, cancer and DNA damage (Malarvizhi et al., 2010;
Wang et al., 2014). Because chromium consists of variable oxidation states in water the guideline value set by World Health
Organization (WHO) regards total chromium concentration,
this value is set to 0.05 ppm. Therefore, it is highly imperative
to treat the water containing chromium before its discharge.
Various treatment techniques including oxidation, reduction, electro-chemical precipitation, ultrafiltration, ion exchange,
reverse osmosis and adsorption have been employed to re-
move chromium in water and wastewater (Rengaraj et al., 2001;
Yurlova et al., 2002). Adsorption on solid surfaces is the most
common one since it is easy to be applied, has a simple design,
and insensitive to toxic substances. Adsorption also offers selectivity in removing low levels of heavy metals from dilute
solutions and environmental friendly if combined with appropriate adsorbent and regeneration steps (Bingöl et al., 2012;
Indah et al., 2017). Many efforts are being made continuously
to develop new, low cost and efficient adsorbents for removal
of metals including chromium. Over the years, the role played
by adsorbents in water and wastewater treatment had been critically and elaborately investigated. Several low cost adsorbents
from agricultural wastes such as rice husk ash (Zhang et al.,
2014) and maize husk (Indah et al., 2016) have been used as
adsorbent. Moreover, the potential the use of natural materials
or local minerals such as zeolite (Motsi et al., 2009) bentonite
(Melichová and Hromada, 2012), and pumice (Sepehr et al.,
2014; Indah et al., 2017) also have been widely considered
because of better performance and low cost of these materials.
Among these natural materials, pumice which is a volcanic
stone and can be found in many regions of the world has a
low weight and a porous structure (up to 85%). Because of its
micro-porous structure, pumice has a high specific surface area,
Indah et. al.
Indonesian Journal of Environmental Management and Sustainability, 2 (2018) 30-27
so that, recently, pumice also has been used as adsorbent for
pollutant removal from water and wastewater (Heibati et al.,
2014).
On the other hands, despite the capability of adsorbents to
remove pollutant in the water, the used adsorbent may generate
a problem to environment because they have to be discarded after it becomes exhausted. In addition, the utilization of mineral
like natural pumice as adsorbent may reduce the availability
of natural resources. Therefore, the regeneration and reuse
of the adsorbents is important to make the operation environmental friendly and minimize the requirement of adsorbent.
In this sense, desorption and reutilization of the adsorbents
in adsorption–desorption cycles could help in reducing the
residues. However, so, far, there is only limited investigations
on the adsorption and desorption as well as regeneration of
natural pumice to remove pollutant in water or wastewater.
Due to several advantages of the pumice and its accessibility
in Indonesia, the main objective of this study was to investigate
its effectiveness for the removal of total chromium at various
experimental conditions and its possibility to reuse after metal
desorption. Laboratory batch experiments were performed
to determine optimal pH, dose of adsorbent, contact time,
diameter of adsorbent, initial concentration of chromium and
the adsorption capacity of pumice. Furthermore, in order to
study regeneration ability of the natural pumice, sequential
adsorption-desorption cycles were conducted 3 times using the
same adsorbent.
2. EXPERIMENTAL SECTION
2.1 Preparation of Adsorbent
Natural pumice sample were obtained from riverside of Sungai
Pasak, West Sumatera, Indonesia as byproduct of the process
of sand mining in that area. Pumice samples were washed with
distilled water several times and dried out at room temperature,
then crushed and sieved in order to obtain the desired particle
size fractions. Energy dispersive x-ray (EDX) spectroscopy
was employed to get information on the oxide content of the
natural pumice. A scanning electron microscopy (SEM, model
S-3400N, Hitachi, Japan) was performed to observe the surface
morphology of pumice.
2.2 Batch Adsorption Experiment
Batch adsorption experiment were conducted at room temperature (25°C) by varying pH, dose of adsorbent, contact
time, diameter of adsorbent and initial concentration of total chromium. In each experiment, in 500 ml erlenmeyer
flasks with 100 ml of chromium solutions was contacted with
pumice and gently agitated at 100 rpm. After a period of time,
the mixture was filtered by using Whatman’s filter paper no
42 and the total chromium concentration in the filtrate was
measured by atomic absorption spectrometry (Rayleigh WFX
320, China). The amount of total chromium adsorbed by the
pumice was generated as the difference between the initial and
final concentration of the solutions. All experiments were performed in triplicate, and results provided are accordingly the
© 2018 The Authors.
averaged values of replicate tests. The adsorption capacity of
total chromium adsorbed (qe , (mg/g)) can be calculated using
the following equation.
qe =
Co − Ce
·V
w
(1)
where Co is the initial concentration of total chromium (mg/L),
Ce is the equilibrium concentration of total chromium g(mg/L),
V is the volume of the solution (L), and W is the mass of the
pumice (g).
2.3 Batch Desoprtion Experiment
The desorption experiment was conducted using pumice with
total chromium adsorbed on the surface at the end of the sorption experiment. Samples were mixed with 0.1 M HCl (a 1:200
solid to solution ratio), shaken at 100 rpm for 60 min and at
room temperature (25°C). Afterwards, the mixture was filtered
by using Whatman’s filter paper no 42 and the total chromium
concentration in the filtrate was measured by atomic absorption
spectrometry (Rayleigh WFX 320, China). All experiments
were repeated three times, and results presented are consequently the averaged values of replicate tests. The desorbed
total chromium was calculated as percentage using equation
(Eq. (2)).
Desorption =
Concentr ationo f desorbedmetal
· 100 (2)
Concentr ationo f adsorbedmetal
3. RESULTS AND DISCUSSION
3.1 Adsorbent Characterization
Si, Al and Fe are the major elements in natural pumice from
Sungai Pasak, as shown in Table 1 as determined by EDX.
Other elements, except K, Ca, Na and Mg were present in
relatively smaller amounts (less than 3%). The elemental compositions of the pumice also indicate the absence of hazardous
or carcinogenic substances, thus the pumice are considered
appropriate as adsorbent to treat polluted water. The SEM
image showed the surface morphology of natural pumice from
Sungai Pasak, West Sumatra was displayed in Figure 1. The
image denoted that the pumice had a highly porous, cellular,
smooth surface, and irregular texture with larger cavities, which
serves suitable sites for adsorption.
3.2 Effect of pH
Many studies have proved that pH is one of the most important
parameters having an influence on the adsorption capacity of
adsorbent for heavy metal ions removal from the aqueous solutions. The effect of pH on the adsorption of total chromium
onto the natural pumice was studied in the range of 2 - 6. Figure 2 shows the total chromium uptake increased from 0.084
mg/g to 0.101 mg/g as pH increased from 2 to 3. The highest
total chromium uptake was recorded at pH 3 and the total
chromium uptake decreased as pH increased to 6. The result
Page 31 of 37
Indah et. al.
Indonesian Journal of Environmental Management and Sustainability, 2 (2018) 30-27
Figure 2. Effect of pH on total Cr uptake onto pumice
(chromium concentration = 0.05 mg/L; adsorbent dose = 0.3
g/L; diameter of adsorbent = < 63 µm; contact time = 60
min). Data represent averages of triplicates ± SE.
Figure 1. SEM micrograph of pumice from Sungai Pasak, West
Sumatra, Indonesia
Table 1. Elemental and oxide composition of natural pumice
from Sungai Pasak, West Sumatra, Indonesia
Element
Na
Mg
Al
Si
K
Ca
Fe
% weight
0.49
0.06
3.89
32.56
2.41
1.2
3
revealed the removal of total chromium from aqueous solution
by adsorption is highly dependent on the pH of the solution,
which affects the surface charge of the adsorbent. At low pH,
the surface of the natural pumice becomes protonated favoring the strong electrostatic attraction between the adsorbent
and chromium anions. However, at higher pH, the binding
sites of adsorbent are deprotonated and causes the increasing
negatively charged sites on the adsorbent surface and this is
no longer favorable to anionic chromium adsorption. Thus,
the optimum pH for adsorption of total chromium onto the
natural pumice was observed at pH 3. Similar finding on pH
trend has been reported in adsorption of chromium studies
by other researchers (Sepehr et al., 2014; Tytłak et al., 2014).
Above all the following experiments were carried out with pH
values of 3.
© 2018 The Authors.
3.3 Effect of Adsorbent Dose
The different doses of the pumice (0.3, 1.0, 3.0, 10 and 30
g/L) were studied to study the effect on chromium adsorption.
The experiment was performed at room temperature, 3 of
pH, 60 minutes of contact time and the initial concentration
of chromium was fixed as 0.05 mg/L (Figure 3). The results
revealed that the chromium uptake decreased as the adsorbent
dose increased. The total chromium uptake decreased from
0.043 mg/g to 0.001 mg/g by increasing the adsorbent dose
from 0.3 to 30 g/L. As the adsorbent dose increased, the sorption sites remain unsaturated during the adsorption reaction
and the agglomeration of adsorbent particles may occur that
reducing the available external surface area and an increase in
diffusional path length both of which contribute to decrease
in amount adsorbed per unit mass. It is in accordance with
our previous study and also confirms observations by other
investigators (Indah et al., 2017; Dhanakumar et al., 2007; Yu
et al., 2003). A maximum adsorption uptake at equilibrium
of 0.043 mg Cr/g was obtained for a pumice dose of 0.3 g/L.
Therefore, 0.3 g/L of adsorbent dose was determined to be
the optimum dose in this study and above all the following
experiments were carried out with this dose.
3.4 Effect of Contact Time
Figure 4 depicts the effect of contact time on the adsorption of
chromium onto natural pumice from aqueous solution. It was
observed that the total Cr uptake increased with increase in contact time up to 60 min. At this time, Cr uptake reached 0.101
mg Cr/g. However, at 90, 120 and 150 min of contact time,
the Cr uptake decreased to 0.09, 0.083 and 0.054 mg Cr/g.
The result indicated that the adsorption of total chromium is
most rapid in the initial stages and gradually decreases until the
equilibrium is reached. A large number of vacant surface sites
of pumice that available for adsorption resulted the increasing
Page 32 of 37
Indah et. al.
Indonesian Journal of Environmental Management and Sustainability, 2 (2018) 30-27
Cr uptake during the initial stage of sorption. After an interval
in time, due to repulsive forces between the solute molecules
on the adsorbent surface and the bulk phase, the remaining
vacant surface sites of pumice were occupied (Wongjunda and
Saueprasea, 2010). Therefore, the equilibrium time for the
removal of total chromium from aqueous solution by natural
pumice is taken as 60 min and applied for further experiments.
3.5 Effect of Diameter of Adsorbent
To study the effect of particle sizes of natural pumice on the
adsorption of total chromium, 5 variations of diameter of adsorbent representing the variation of particle size of adsorbent
were applied. Figure 5 shows that the increasing in the diameter of adsorbent resulted the decreasing in total Cr uptake. The
total Cr uptake was decrease from 0.103 to 0.053 mg Cr/g as
diameter of adsorbent increase from <63 to 500-600 µm. The
results revealed that the adsorption capacity depends on the
size of adsorbent; as the diameter of adsorbent decreases, the
adsorption capacity increases due to the wider exchange surface
provided for the adsorption of the chromium ions. Similar
results were also documented in in the literature using other adsorbent [2, 17] (Wang et al., 2014; Lopez-Nuñez et al., 2014).
Therefore <63 µm, as the smallest diameter of the 5 variations,
was defined as the optimum diameter of adsorption and were
applied for the further experiments.
3.6 Effect of Initial Concentration
The effect of initial concentration on total chromium adsorption onto natural pumice was investigated in the range 0.01-1
mg/L. As shown in Figure 6, the total Cr uptake increased from
0.012 to 2.226 mg Cr/g, as the concentration was increased
from 0.01 to 1 mg/L. It indicated that the actual amount of
chromium ions adsorbed per unit mass of the natural pumice
was increased with increasing in chromium ions concentra-
Figure 4. Effect of contact time on total Cr uptake onto pumice
(chromium concentration = 0.05 mg/L; diameter of adsorbent
= < 63 µm; pH = 3; adsorbent dose = 0.3 g/L). Data
represent averages of triplicates ± SE.
tion in the aqueous solution. An increase in initial chromium
concentration may cause higher availability of chromium ions
in the solution for removal and increase concentration gradient, which provides a stronger driving force to overcome mass
transfer resistance of chromium ions between the aqueous and
solid phases, resulting in higher probability of collision between
chromium ions and active sites of natural pumice, thus leading to a higher total chromium uptake. The results clarified
that higher initial concentration of chromium can enhance
the adsorption process and the interaction between chromium
and pumice as adsorbent. The result is consistent with the
finding by other researchers (Malarvizhi et al., 2010; PuentesCárdenas et al., 2012). From the results it was also evident
that the adsorption of total chromium onto natural pumice is
dependent on initial metal concentration. Under the conditions tested in this study, the highest total chromium uptake
was 2.226 mg Cr/g.
3.7 Adsorption Isotherm Models
The adsorption isotherm usually shows how the molecules are
distributed between the liquid and the solid phases, at equilibrium during the adsorption process. A number of isotherm
models have been developed to describe equilibrium relationships. Linear forms of the Langmuir, Freundlich and Elovich
adsorption isotherm models ((3), (4) and (5), respectively) were
used to verify the adsorption data:
Figure 3. Effect of adsorbent dose on total Cr uptake onto
pumice (chromium concentration = 0.05 mg/L; diameter of
adsorbent = < 63 µm; pH = 3; contact time = 60 min). Data
represent averages of triplicates ± SE
© 2018 The Authors.
Ce
Ce
1
=
+
qe
qmax KL qmax
log qe = log KF +
1
log Ce
n
(3)
(4)
Page 33 of 37
Indah et. al.
Indonesian Journal of Environmental Management and Sustainability, 2 (2018) 30-27
Figure 5. Effect of diameter of absorbent on total Cr uptake
Figure 6. Effect of initial concentration on total Cr uptake onto
onto pumice (chromium concentration = 0.05 mg/L; pH = 3;
adsorbent dose = 0.3 g/L; contact time = 60 min). Data
represent averages of triplicates ± SE.
pumice (pH = 3; adsorbent dose = 0.3 g/L; contact time = 60
min; diameter of adsorbent = < 63 µm). Data represent
averages of triplicates ± SE.
Table 2. Isotherm model constants for adsorption of total
qe
qe
ln
= ln KE qmax −
Ce
qmax
(5)
where Ce is the equilibrium concentration, qe is the amount
of adsorbate adsorbed per unit mass of adsorbent, qmax is the
maximum adsorption capacity, KL is the Langmuir constant
related to the adsorption rate, KF is the Freundlich isotherm
constant related to adsorption capacity, n is the Freundlich
isotherm constant related to adsorption intensity (indicating the
favourability of the adsorption process) and KE is the Elovich
equilibrium constant.
The Langmuir model assumes uniform energies of adsorption onto the surface and no transmigration of the adsorbate
along the plane of the surface. From the slopes and the intercepts, a linear fit to the Langmuir equation yields Langmuir
constant (KL ) and the maximum adsorption capacity (qmax ),
respectively (Low, 1960). The Freundlich model is based on
the assumption that as the adsorbate concentration increases,
the concentration of adsorbate on the adsorbent surface also
increases. The linear form of the Freundlich isotherm model
yields a straight line. The slope and intercept of the obtained
fit are used to calculate the Freundlich constants 1/n and KF
(Freundlich, 1907). The Elovich model is based on a kinetic
principle assuming that the adsorption sites increase exponentially with adsorption, which implies a multilayer adsorption.
The Elovich maximum adsorption capacity and Elovich constant can be calculated from the slopes and the intercepts of the
plot of ln(qe /Ce ) versus qe (Elovich and Larinov, 1962). The applicability of the isotherm equations to describe the adsorption
process was judged based on the maximum value of adsorption and correlation coefficients (R 2 ) which are a measure of
goodness of fit.
To determine the adsorption isotherm of total chromium
adsorption onto natural pumice, the initial total chromium
© 2018 The Authors.
chromium onto natural pumice
Isotherm
Langmuir
Freundlich
Elovich
Constants
qmax (mg/g)
-1
1/n
1.33
qmax (mg/g)
-1.98
KL (L/mg)
-2.31
KF (L/g)
9.25
KE (L/mg)
0.63
R2
0.687
0.99
0.746
concentration was varied in the interval ranging from 0.01 to
1 mg/L with 3 of pH and 0.3 g/L of adsorbent dose. Figure 7 shows the Langmuir, Freundlich and Elovich isotherm
plots and Table 2 presents the isotherm model constants for
the adsorption. Data in Table 2 show that the Freundlich
isotherm model presents the highest R 2 value (0.990) indicated
the model fitted well with the equilibrium data, compared with
Langmuir and Elovich isotherm models. It revealed that the
adsorption of total chromium onto natural pumice is multilayer
sorption and the adsorption occurred on the heterogeneous
surface of pumice and the active sites of pumice have different
energy, as the Freundlich isotherm model’s assumption [20].
As shown in Table 2, for the Langmuir model, the maximal value of adsorption qmax was negative, which reflects the
inadequacy of this model for explaining the adsorption process (Alshabanat et al., 2013). From the Freundlich isotherm
model, the adsorption of total chromium onto natural pumice
from Sungai Pasak resulted 9.25 mg Cr/g of KF as adsorption
capacity and 1.33 of 1/n. The 1/n value derived from the
Freundlich equation serves to describe the linearity of adsorption. Typically, 1/n values range from 1 downwards. A higher
value of n (smaller value of 1/n) implies an effective interacPage 34 of 37
Indah et. al.
Indonesian Journal of Environmental Management and Sustainability, 2 (2018) 30-27
Figure 8. Adsorption and desorption efficiencies as well as total
Figure 7. Langmuir (a), Freundlich (b) and Elovich (c) isotherm
plots for the adsorption of Cr onto natural pumice (Cr
concentration: 0.01-1 g/L; adsorbent dose: 0.3 g/L; contact
time: 60 min; pH: 3)
tion between the adsorbent and adsorbate. When 1/n < 1, it
corresponds a normal L-type Langmuir adsorption isotherm,
while 1/n > 1 reflects a co-operative adsorption (Guo et al.,
2016). Since the value of 1/n from this study is 1.33, it indicate
that co-operative adsorption may occur in the system, where
adsorbed adsorbate has an effect on the adsorption of “new” adsorbate molecules. Moreover, 1/n values of > 1 are indicative
of S-type isotherms, according to the Giles et al. (Giles et al.,
1960) classification, indicating that adsorption becomes easier
for increasing concentration. The S-type characterized first by
a weak adsorption which then gradually increases suggests a
weak surface interaction and competitive adsorbate-adsorbate
interactions. The S curve of the adsorption isotherm generally reflects strong competition between the solvent and the
adsorbed species for the adsorbent surface sites. For this study,
in order to make a stronger interaction between natural pumice
as adsorbent and adsorbate, more attempts could be made,
such as modify the surface of the adsorbent physically or chemically using thermal treatment, protonation or metal oxides
impregnation (Sepehr et al., 2014).
3.8 Desorption Study
Batch desorption experiments were conducted in order to investigate the mechanism of metal ion removal and recovery
from metal-loaded adsorbent and also for the regeneration and
recycling of spent adsorbents, which in turn may reduce operational cost and protect the environment from the problem
of residues of the adsorbent. In addition, efficient removal of
loaded metal from the natural pumice was necessary to ensure
its long term use for repeated adsorption-desorption cycles.
The regeneration of the adsorbent is likely to be a key factor in
© 2018 The Authors.
Cr uptake onto pumice at 3 cycles of adsorption-desorption
(pH = 3; adsorbent dose = 0.3 g/L; contact time = 60 min;
diameter of adsorbent = <63 µm; chromium concentration =
1 mg/L). Data represent averages of triplicates ± SE
accessing the potential of the adsorbent for commercial application. The capacity of natural pumice to adsorb total chromium
ions was determined by repeating the adsorption-desorption
experiments in three consecutive cycles by using 0.1 M HCl as
desorbing agent.
Figure 8 shows the desorption efficiencies for total chromium
ions by using 0.1 M HCl as desorbing agent were in the range
of 31-32%. A slight increase in desorption efficiencies was
observed (approximately 1 %) at the second desorption cycle
(desorption 2) may due to the accumulation of total chromium
ions that could not release at the second adsorption (adsorption
2). Although complete desorption were not achieved, the result
confirmed that HCl can be used as desorbing and recovery
agent. In desorption process, the residence time is very essential because the higher the residence time, the longer the contact
between the desorbing agent and the metal loaded adsorbent, so
that the desorption efficiency may increase (D Wankasi, 2005).
Desorption efficiency of Cr(VI) ion from natural pumice obtained from Tikmeh Dash Reign, East Azerbaijan, Iran reached
94.3% after 300 min contact time with 1 M HCl (Sepehr et al.,
2014). In this study, the desorption time was 60 min. If the
contact time is extended, it may be possible to reach 100%
desorption.
As shown in Figure 8, the reuse of the remaining natural
pumice in a second and third adsorption cycle increased the
removal efficiency of total chromium ions from 63.50% (adsorption 1) to 73.47% (adsorption 2) and 78.66% (adsorption
3). These results may be related to chemical changes in the
natural pumice produced by acid solution (HCl) that used as
desorbing agent. Many researchers notified that the interaction
between acid solution like HCl and adsorbents can modify the
adsorbents and improve their adsorption capacity. The acid
solution can removal of impurities on the adsorbent surface,
Page 35 of 37
Indah et. al.
Indonesian Journal of Environmental Management and Sustainability, 2 (2018) 30-27
decrease the organic content, increase the porosity, breakdown
of the cell wall or generation of new sorption active sites of the
adsorbents (Sepehr et al., 2014). These results define that natural pumice from Sungai Pasak, West Sumatra, Indonesia can
be sufficiently reused up to 3 cycles of adsorption- desorption.
D Wankasi, A. S., M Horsfall Jnr (2005). Desorption of Pb2+
and Cu2+ from Nipa palm (Nypa fruticans Wurmb) biomass.
African Journal of Biotechnology, 4(9); 923–927
Dhanakumar, S., G. Solaraj, R. Mohanraj, and S. Pattabhi
(2007). Removal of Cr (VI) from Aqueous Solution by
Adsorption Using Cooked Tea Dust. Indian Journal of Science
and Technology, 1(2); 1–6
4. CONCLUSIONS
Elovich,
S. and O. Larinov (1962). Theory of Adsorption from
Natural pumice from Sungai Pasak, West Sumatra, IndoneSolutions
of Non Electrolytes on Solid (I) Equation Adsorpsia, which is available in a great abundance, as by-product of
tion
from
Solutions and the Analysis of Its Simplest Form,
the process of sand mining in that area, was examined to be(II)
Verification
of the Equation of Adsorption Isotherm
come an alternative low-cost adsorbent for the removal of total
from
Solutions.
Izvestiya Akademii Nauk SSSR, Otdelenie
chromium in water. The natural pumice has a highly porous,
Khimicheskikh
Nauk,
2; 209–216
smooth surface, cellular and irregular texture with larger cavFreundlich,
H.
(1907).
Über die Adsorption in Lösungen.
ities, which provides suitable sites for adsorption. From the
Zeitschrift
für
Physikalische
Chemie, 57U(1)
batch experiments which were performed at ambient temperaGiles,
C.
H.,
T.
H.
MacEwan,
S. N. Nakhwa, and D. Smith
◦
ture (25 C) and 100 rpm of agitation speed, it was found that
(1960).
Studies
in
adsorption.
Part XI. A system of clasthe optimum condition of total chromium removal by natural
sification
of
solution
adsorption
isotherms, and its use in
pumice were 3 of pH solution, 0.3 g/L of adsorbent dose, 60
diagnosis
of
adsorption
mechanisms
and in measurement of
min of contact time of adsorption, <63 µm of diameter of
specific
surface
areas
of
solids.
Journal
of the Chemical Society
adsorbent, and 1 mg/L of total Cr concentration with 2.226
(Resumed);
3973
mg Cr/g pumice of adsorption capacity. The result also reGuo, W., Z. Wu, S. Hu, L. Jin, K. Qiu, Q. Guo, and Y. Gan
vealed that the Freundlich isotherm model fitted well with the
(2016). Gas collision for improving the precision and accuequilibrium data within the concentration range studied as it
racy of 11B/10B ratios determination in ICP-QMS and its
presents higher R 2 value than that of the Langmuir and Elovich
application to determining wine provenance. RSC Advances,
isotherms. It denoted that the adsorption of total chromium
6(53); 47394–47401
onto natural pumice is multilayer sorption, the adsorption ocHeibati,
B., S. Rodriguez-Couto, A. Amrane, M. Rafatullah,
curred on the heterogeneous surface of pumice and the active
A.
Hawari,
and M. A. Al-Ghouti (2014). Uptake of Reactive
sites of pumice have different energy. To maximize function
Black
5
by
pumice and walnut activated carbon: Chemistry
and capability of adsorbent used and make the process enviand
adsorption
mechanisms. Journal of Industrial and Engironmental friendly, the regeneration and reuse of adsorbent
neering
Chemistry,
20(5); 2939–2947
were studied by desorption experiment. It was confirmed that
Indah,
S.,
D.
Helard,
T. Edwin, and R. Pratiwi (2017). Utithe exhausted natural pumice could be desorbed 31-32% by
lization
of
pumice
from
Sungai Pasak, West Sumatera, In0.1 M HCl. The used natural pumice also could be regenerdonesia
as
low-cost
adsorbent
in removal of manganese from
ated and reused up to three successive adsorption-desorption
aqueous
solution.
Author(s)
cycles with increasing trend in total Cr uptake that may due to
Indah, S., D. Helard, and A. Sasmita (2016). Utilization of
the surface modification of natural pumice caused by HCl as
maize husk (Zea mays L.) as low-cost adsorbent in removal
acidic medium. Overall study revealed that pumice from Sunof iron from aqueous solution. Water Science and Technology,
gai Pasak could be a promising adsorbent for total chromium
73(12);
2929–2935
removal from water.
Lopez-Nuñez, P. V., E. Aranda-García, M. d. C. CristianiUrbina, L. Morales-Barrera, and E. Cristiani-Urbina
5. ACKNOWLEDGEMENT
(2014). REMOVAL OF HEXAVALENT AND TOThe authors would like to thank Faculty of Engineering, UniverTAL CHROMIUM FROM AQUEOUS SOLUTIONS BY
sitas Andalas, Indonesia (Grand No. 045/UN16.09.D/PL/2017)
PLUM (P. domestica L.) TREE BARK. Environmental Enfor supporting this work
gineering & Management Journal (EEMJ), 13(8)
Low, M. J. D. (1960). Kinetics of Chemisorption of Gases on
REFERENCES
Solids. Chemical Reviews, 60(3); 267–312
Malarvizhi,
R., Y. Venkateswarlu, V. R. babu, and S. S. Begum
Alshabanat, M., G. Alsenani, and R. Almufarij (2013). Re(2010).
Studies
on removal of chromium (VI) from water
moval of Crystal Violet Dye from Aqueous Solutions onto
using
chitosan
coated
Cyperus pangorei. Water Science &
Date Palm Fiber by Adsorption Technique. Journal of ChemTechnology,
62(10);
2435
istry, 2013; 1–6
Bingöl, D., M. Hercan, S. Elevli, and E. Kılıç (2012). Com- Melichová, Z. and L. Hromada (2012). Adsorption of Pb2+
and Cu2+ Ions from Aqueous Solutions on Natural Benparison of the results of response surface methodology and
tonite.
22; 457–464
artificial neural network for the biosorption of lead using
Motsi,
T.,
N. Rowson, and M. Simmons (2009). Adsorption
black cumin. Bioresource Technology, 112; 111–115
© 2018 The Authors.
Page 36 of 37
Indah et. al.
Indonesian Journal of Environmental Management and Sustainability, 2 (2018) 30-27
of heavy metals from acid mine drainage by natural zeolite.
International Journal of Mineral Processing, 92(1-2); 42–48
Puentes-Cárdenas, I. J., A. M. Pedroza-Rodríguez,
M. Navarrete-López, T. L. Villegas-Garrido, and
E. Cristiani-Urbina (2012).
BIOSORPTION OF
TRIVALENT CHROMIUM FROM AQUEOUS SOLUTIONS BY Pleurotus ostreatus BIOMASS. Environmental
Engineering & Management Journal (EEMJ), 11(10)
Rengaraj, S., K.-H. Yeon, and S.-H. Moon (2001). Removal
of chromium from water and wastewater by ion exchange
resins. Journal of Hazardous Materials, 87(1-3); 273–287
Sepehr, M. N., A. Amrane, K. A. Karimaian, M. Zarrabi, and
H. R. Ghaffari (2014). Potential of waste pumice and surface modified pumice for hexavalent chromium removal:
Characterization, equilibrium, thermodynamic and kinetic
study. Journal of the Taiwan Institute of Chemical Engineers,
45(2); 635–647
Tytłak, A., P. Oleszczuk, and R. Dobrowolski (2014). Sorption
and desorption of Cr(VI) ions from water by biochars in
different environmental conditions. Environmental Science
© 2018 The Authors.
and Pollution Research, 22(8); 5985–5994
Wang, Q., N. Chen, Y. Yu, C. Feng, Q. Ning, and W. Hu
(2014). Chromium(VI) removal from aqueous solution using a new synthesized adsorbent. Desalination and Water
Treatment; 1–11
Wongjunda, J. and P. Saueprasea (2010). Biosorption of
Chromium (VI) Using Rice Husk Ash and Modified Rice
Husk Ash. Environmental Research Journal, 4(3); 244–250
Yu, L. J., S. S. Shukla, K. L. Dorris, A. Shukla, and J. Margrave
(2003). Adsorption of chromium from aqueous solutions
by maple sawdust. Journal of Hazardous Materials, 100(1-3);
53–63
Yurlova, L., A. Kryvoruchko, and B. Kornilovich (2002). Removal of Ni(II) ions from wastewater by micellar-enhanced
ultrafiltration. Desalination, 144(1-3); 255–260
Zhang, Y., J. Zhao, Z. Jiang, D. Shan, and Y. Lu (2014).
Biosorption of Fe(II) and Mn(II) Ions from Aqueous Solution by Rice Husk Ash. BioMed Research International, 2014;
1–10
Page 37 of 37