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Research
paper / Art’culo cient’fico
 =
;
Analysis and risk assessment of arse=
nic
in the water sources of the cities Cuenca and Azogues, Ecuador
<=
i
style=3D'mso-bidi-font-style:normal'>An‡lisis y evaluaci—n de riesgos de arsŽnico en las
fuentes de agua de las ciudades
de Cuenca y
Azogues, Ecuador
Guillermina Pauta1*
, Mar’a Velasco2,
Gabriela V‡zquez1
, Andrea Abril1
, <=
/b>
Santiago
Torres 3
1 Departamento de Ingenier’a Civil, Universidad de Cuenca, Cuenca,
Ecuador.
2 Instituto Ecuatoriano de Seguridad Social, Cuenca,
Ecuador.
3 Facultad de Ciencias Agropecuarias, Universidad de
Cuenca, Cuenca, Ecuador.
<=
span
lang=3DEN-US style=3D'mso-bidi-font-size:9.0pt'>* Corresponding author: guillermina.pauta@=
ucuenca.edu.ec
Reception date=
: June
29, 2021 Ð Acceptance date: August 3, 2021
ABSTRACT
Arsenic (As) is a toxic
element present in the environment posing a threat to consumers health. To
identify the arsenic content in rivers, p‡ramos, and wells in the city of
Cuenca, and in rivers in the city of Azogues, two monitoring campaigns in th=
e
period August-November 2017 were conducted, respectively during a low and hi=
gh
flow hydrological period. The measurements encompassed physicochemical quali=
ty
indicators such as pH, color, turbidity, and conductivity. Results show that
the p‡ramos and wells are free of As, while this toxic substance is present =
in
surface water with higher levels in periods of high flow. A significant
association between the concentration of As and the pH of river water was
found. The risk of chronic toxicity from consumption is almost non-existent
because the observed As levels exceed only
exceptionally the permissible limit established by the Ecuadorian TULSMA
(Unified Text of Secondary Environmental Legislation) regulation. The presen=
ce
of As in surface water is the result of
anthropological activities such as the use of pesticides. A permanent
monitoring of the quality of water resources for human consumption is
necessary, particularly in the rainy season, due to the diffuse and difficul=
t
to control pollution processes.
Keywords :
Arsenic, water sources, river, groundwater, p‡ramo, chronic toxicity.=
o:p>
RESUMEN
El arsŽnico (As) es un elemento
t—xico presente en el medio ambiente que representa una amenaza para la salu=
d
de los consumidores. Para identificar el contenido de arsŽnico en r’os, p‡ra=
mos
y pozos de la ciudad de Cuenca, y en r’os de la ciudad de Azogues, se realiz=
aron
dos campa–as de monitoreo en el per’odo agosto-noviembre de 2017, durante un
per’odo hidrol—gico de bajo y alto caudal, respectivamente. Las mediciones
abarcaron indicadores de calidad fisicoqu’mica como pH, color, turbidez y
conductividad. Los resultados muestran que los p‡ramos y pozos est‡n libres =
de
As, mientras que esta sustancia t—xica est‡ presente en aguas superficiales =
con
niveles m‡s altos en per’odos de alto caudal. Se encontr— una asociaci—n
significativa entre la concentraci—n de As y el pH del agua del r’o. El ries=
go
de toxicidad cr—nica por consumo es casi inexistente porque los niveles de A=
s
observados superan solo excepcionalmente el l’mite permisible establecido po=
r
el reglamento ecuatoriano TULSMA (Texto Unificado de Legislaci—n Ambiental
Secundaria). La presencia de As en aguas superficiales es el resultado de
actividades antropol—gicas como el uso de pesticidas. Es necesario un monito=
reo
permanente de la calidad de los recursos h’dricos para consumo humano,
particularmente en la Žpoca de lluvias, debido a los procesos de contaminac=
i—n
difusos y dif’ciles de controlar.
Palabras clave : ArsŽni=
co,
fuentes de agua, r’o, agua subterr‡nea, p‡ramo, toxicidad cr—nica.
1. =
INTRODUCTION
1=
.1. =
Antecedents
Long-term consumption of As contaminated w=
ater
is harmful (Lillo, 2008) and can cause distinct types of cancer, premature
birth, diabetes, and adverse effects on the skin, nervous system and liver
(Moreno, 2003; Ng, Wang, & Shraim, 2003). Sources of As
are natural contamination of geological (Salom—n, Guam‡n, Rubio, Gal‡rraga,
& Abraham, 2008) and/or anthropogenic origins such as mining, agricultur=
e,
and industry. The quality of water supply is a concern since supplies come=
span>
from surface bodies and
underground reserves. Arsenic disturbs the ecosystem; it is a carcinogenic
substance classified by the WHO (2011) as one of the ten most dangerous. The
TULSMA regulation sets maximum limits for the main uses of water, and the Ec=
uadorian
Technical Standard INEN (1108) defined 10 _g As /L=
as
the maximum allowable concentration in drinking water. The presence of As in water supply should be monitored (Ma–ay, Pist—n,
C‡ceres, Pizzorno, & BŸhl, 2019) especially in rural environments, where
the chemical quality can be seriously compromised by the existence of toxic
substances, such as pesticides. IARC (2018) classifies A=
s
in group 1 of carcinogenic substances, and it is considered a public health
problem that must be controlled to ensure safe water consumption (Carabantes
& De Fernicola, 2003). The results of this research will be transferred =
to
the water managers and will be used for the implementation of public policie=
s
aimed at protecting the health of the population.
=
1.2. Fundam=
entals
and bibliographic review
Origin, entry routes, and levels of As
Naturally occurring As can aff=
ect
large areas, whereas anthropogenic contamination is in general limited in ar=
eal
extent. According to Lillo (2008) and Delgado, Medina, Vega, Carretero, &=
;
Pardo (2009) is natural contamination of aquifers not governed by common
geological/hydrogeological models. Arsenic is a chemical element that man
neither creates nor destroys but introduces into the environment, altering t=
he
chemical and biochemical form in which it is found (Moreno, 2003). Human
exposure is through the consumption of drinking water, although diet (ELIKA,
2013) and inhalation may contribute as well. In areas with arsenical waters,
vegetables and livestock are also affected (Galindo, Fern‡ndez, Parada, &=
;
Gimeno, 2005).
The highest levels of As have =
been
recorded in groundwater in several countries, exceeding the WHO 2018 guideli=
ne
of 10 _g As/L for drinking water, and aquifers of different depths and under
both reducing and oxidizing conditions (Lillo, 2008; Mayorga, 2013). It occu=
rs
in organic and inorganic form, the latter being highly toxic and carcinogeni=
c,
while in organic form As is less toxic since it i=
s
more easily excreted, but tends to accumulate in tissues and organs producin=
g
chronic toxicity (ELIKA, 2013; Ram’rez, 2013).
Forms of As
The oxidized forms dominate in surface water and the redu=
ced
more toxic forms in subterranean aquifers (Bundschub, PŽrez, & Litter,
2008). The main mineral of arsenic is FeAsS (arsenopyrite) although it can
occur in other metallic arsenites forms (Gonz‡lez-ValdŽz et al. , 2011=
).
In surface and groundwater, the oxidation states are commonly As+5
and As+3 and less frequently As0 and
As-3 (WHO, 2011; Souza, Borges, Braga, Veloso,
& Matos, 2019). Arsenite (As+3 ) is found in groundwater with =
a
pH of 5 to 9 and arsenate (As+5 ) in surface waters with high oxyg=
en
levels as H3 AsO4 in the pH range 2 to 13 (Shi, 2004). =
In
well-oxygenated natural waters, the most abundant form is soluble arsenate,
more thermodynamically stable than arsenite (Genc, Tjell, McConchie, &
Schuilling, 2003; Castro, 2004).
Factors
determining the mobilization of As in groundwater=
The soluble species of As in a
natural environment are controlled by the combination of several factors suc=
h
as:
á&nbs=
p;
The adsorption and
desorption conditions on the surface of the minerals. Hydroxy groups on the
surface of certain minerals and reactive adsorption sites are more abundant,
particularly on iron, aluminum, and magnesium oxides and hydroxides possessi=
ng
a strong affinity for As +5 . Under
moderately reducing conditions, the solubility of As
can be conditioned by the dissolution and/or desorption of oxyhydroxides
(Mayorga, 2013). The reduction of the specific surface and the charge in the
solid phase of oxides and hydroxides of Fe constitute other desorption
mechanisms.
á&nbs=
p;
The redox potential o=
f
the medium. Sulfide oxidation mobilizes As only
locally in sulfide-rich mining areas and under oxidizing conditions. Dissolv=
ed
Fe tends to precipitate into ferric sulfate, oxides, and oxyhydroxide, with
re-adsorption and co-precipitation of As ; pyrite
oxidation is not considered the most efficient mechanism in terms of As
mobilization (Lillo, 2008).
á&nbs=
p;
The pH of the solutio=
n.
As is mobilized at pH values of groundwater in the range 6.5-8.5 (Lillo, 200=
8);
adsorbs very strongly to the surfaces of iron oxides in acidic waters or wit=
h a
neutral pH and desorbs when the pH becomes alkaline. This process, being one=
of
the most effective mechanisms in its mobilization, is accompanied with a
positive correlation between the As concentration=
in
the aqueous phase and the pH (Mej’a, Gonz‡lez, Briones, Cardona, & Soto,
2014). Alkalinization of the soil contributes to the mobility of As (Moreno, 2003), and diagenetic processes enhance the
evolution of groundwater towards alkaline conditions leading to the desorpti=
on
of As (Lillo, 2008).
á&nbs=
p;
Competition for
adsorption sites. Bicarbonate ion displaces arsenites and arsenates adsorbed=
on
ferrihydrite (Mayorga, 2013), and overexploitation of aquifers mobilizes As.=
á&nbs=
p;
Microbiological
activity. The microorganisms reduce the insoluble Fe+3 from the
solid phase to the soluble Fe+2 form, mobilizing and reducing As +5 to As+3 (Mayorga, 2013).
á&nbs=
p;
Presence of organic
matter. There are bacteria that oxidize organic matter through the consumpti=
on
of nitrates and in turn oxidize soluble Fe and As =
to
respectively Fe+3 , Fe+4 and As+5 (Machado,
BŸhl, & Ma–ay, 2019). Furthermore, fulvic and humic acids compete for th=
e
adsorption sites of As in iron minerals (hematite=
s)
(Mayorga, 2013).
<=
span
lang=3DEN-US style=3D'font-size:9.0pt;font-family:"Times New Roman";mso-ansi=
-language:
EN-US'>
Toxicology of As =
i>
The half-life time of inorganic As
in humanÕs is 10 hours. Its biotransformation involves the reduction of As to acidic metabolites that are efficiently excreted;=
and
continuous exposure results into the accumulation in certain tissues, affect=
ing
NADH (nicotinamide adenine dinucleotide) (Moreno, 2003), DNA (WHO, 2018;
Markowski, Currie, Reeve, & Thompson, 2010), and increasing the risk for
the development of type II diabetes (Arias, 2016). WHO estimates that for As to be harmful an exposure of 5 to 10 years is requir=
ed
depending on the concentration, and estimates that more than 30 million peop=
le
consume water with an As content above the permissible limit (WHO, 2018).
=
1.3. Genera=
l
objective
The study contributes to the existing knowledge of the
quality of water destined for human consumption by searching for toxic
substances, such as arsenic, whose presence represents a danger to the healt=
h
of the people that consumes water without prior treatment. In particular, th=
e
study aimed the development of a database of arsenic levels in selected wate=
r
sources in the Ecuadorian cities Cuenca and Azogues to know their contaminat=
ion
level, define the relationship between As levels =
and
physicochemical quality parameters, and analyze As contamination risk
situations in groundwater and contaminated surface water sources. =
=
2. &n=
bsp; MATERIALS
AND METHODS
=
2.1. Identi=
fication
of monitoring stations
The study consisted of specific actions in four rivers
crossing the city of Cuenca, in the Quimsacocha p‡ramos, irrigation wells of
the University of Cuenca, and in the Burgay and Tabacay rivers of the city o=
f
Azogues. All these water sources are representative for the water used in th=
e
local water distribution system. For the assessment of the river water,
stations were selected that allow interpreting the quality along the course =
of
the rivers, starting in the high areas with little urban and industrial
influence, passing through highly populated areas to finally form the Cuenca
River, an important tributary of the Paute River, the hydrographic artery in
the south of Ecuador. The monitoring points are identified as: Rio Tomebamba=
TO
with 7 stations; River Yanuncay Y with 7; R’o Tarqui TA with 7
stations; R’o Mach‡ngara MA with 5; the par‡mos of Quimsacocha Q=
b>
with 2 points; 5 groundwater wells W ; R’o Burgay B with 6; and
the R’o Tabacay TB with 6 stations. A total of 90 samples were analyz=
ed
spread over two campaigns in the period August-November 2017.
=
2.2. Method=
ology
for water quality determination
For=
the
determination of the pH, conductivity, apparent and real color, and turbidit=
y
we used the methods published in the 22nd Edition of the Standard
Methods for the evaluation of Water and Wastewater (American Water Works Association, 2012) , and for the
determination of the As concentration the A=
rsenator
Wagtech Palintest =
- Model WAG-WE1000143 instrument
was used. To check the results, double samples were analyzed by the Silver Diethyldithiocarbamate (SDDC) method . <=
/h1>
=
2.3. Regula=
tions
pertaining to water use
Specifications of the quality of water sources for respec=
tively
human and domestic consumption is 0,01 mg/L, the preservation of aquatic lif=
e
0.05 mg/L, for irrigation water 0.1 mg/l, livestock use 0.2 mg/L, and for
groundwater 0.035 mg/L (TULSMA, 2009) (see Ecuadorian TULSMA Regulations,
Special Edition No. 387 GOB.EC (2015), BOOK VI, ANNEX 1). <=
/p>
=
2.4. Method=
ology
for predicting toxicological risk
The used approach is based on Pauta (2014) and consists o=
f
mathematical calculations for the prediction of the chronic effect that woul=
d
be produced by continuous ingestion of a contaminant.
Cancer risk index <=
/i>
The probability that cancer occurs as a consequence of
exposure to a pollutant (Moreno, 2003) is calculated with the following
equation:
=
(Equation 1)
where LADD stands for the lifetime average daily dose, it=
is
the daily dose of the toxic element that a person would receive throughout h=
is
life if the exposure were continuous at a given concentration. The latter is
calculated using Equation 2:
=
&n=
bsp; =
&nbs=
p; (Equation
2)
where CT is the concentration in water of the toxic
substance (mg/L); TC the contact rate equal to 2 L/person-day (EPA); B the
bioavailability (0.7 for As in drinking water); P=
E the
exposure period in years; FE the frequency of exposure in days/year; and PC =
the
body weight in kg/person. The slope factor in Equation 1 represents the
relationship between the dose of carcinogen and the incidence of tumors
(Moreno, 2003), while the permitted daily dose for a given risk stands for t=
he
intake of As in water for a risk of 1 E-6
(the possibility that a person per million contracts cancer), which can be
calculated by Equation 3:
<=
span
lang=3DEN-US style=3D'font-size:9.0pt;mso-bidi-font-size:11.0pt;line-height:=
107%;
font-family:"Times New Roman";mso-fareast-font-family:Calibri;mso-fareast-th=
eme-font:
minor-latin;mso-bidi-theme-font:minor-bidi;mso-ansi-language:EN-US;mso-farea=
st-language:
EN-US;mso-bidi-language:AR-SA'> =
(Equation 3)
where the permitted daily dose =3D 2 E-5 mg As /L * 2 L/person-day-70 kg person =3D 5.71 E-7
mg/day-kg. If the calculated risk is >1 means that the probability of dev=
eloping
cancer is greater than that calculated for a unit per million inhabitants.
Criteria for calculating the
toxicological risk
To calculate the risk to which humans are exposed by the
continuous consumption (for a period of 25 years) of water contaminated with
As, it is considered that the route of exposure to the poison involves direc=
t
contact, from the source to the human organism and taking as a reference EPA
toxicological data and the Toxicological Databases: Weight of Evidence (WoE)=
=3D
1 A; Oral Slope Factor =3D 1.5 mg/kg-day; risk level =3D 1 E-6 (1=
of
every million inhabitants); and permitted concentration for this risk level =
= 2
E-5 mg As/L.
=
3. &n=
bsp; RESULTS
Table 1 presents the results of the water quality in the =
two
hydrological periods of monitoring, and Table 2 shows the results of the Can=
cer
Risk Index for the As concentration in the last
monitoring station of the Tomebamba river applying Equation 1. The cancer ri=
sk
index is >1, only in the last station of the Tomebamba river with a value=
of
1.36. This means that if the water were consumed without prior treatment for=
25
years, not just one person would get cancer in a million population but 1.36
people. In the other stations, the index is less than 1. =
p>
4.=
&n=
bsp; STATISTICAL
ANALYSIS AND DISCUSSION
The statistical interpretation of the registered As levels for different flow rates is shown in Table 3.=
The
Machangara and Tarqui rivers do not register As values in the low flow regim=
e
(LF ) but the toxic substanc=
e
is detected in the high flow regime (HF1 ). The average levels
present a high variability between the separate places, as depicted in Figur=
e
1. During HF was the highest average value found in the Burgay river (6.8
µg/L), and the highest maximum value in the Tomebamba river (28 µg/L ) . In the dry season (LF), the hi=
ghest
average value was for the Yanuncay river (6.6 µg/L), and the maximum
concentration of As was found in the Tomebamba ri=
ver (8
µg/L ). The statistical behavior reflected the
absence of normality, justifying the use of the Shapiro Wilk test which is
significant in all observed cases (p <0.05), and permitting the
application of nonparametric statistics such as the percentiles and the
Spearman rank correlation test.
The level of As during HF in t=
he
Tomebamba river varies statistically from 0 to 28 _g/L, the latter being the
highest observed level which exceeds the reference norm of 10 _g/L for human
consumption. On the other hand, during LF the maximum levels that occur in t=
he
Tomebamba and Burgay rivers, respectively 8 and 6.6 _g/L, do not exceed the
reference norm. The intervals that allow determining the parameter of As in each place are smaller during HF, which would imp=
ly in
general lower levels of As during LF.
=
A high positive and
significant correlation between As levels and the
physical-chemical quality parameters of water is observed during HF; accordi=
ng
to the Spearman statistics (p <0.05) between As and pH. The
correlations between turbidity, color, and temperature with the As level are also high (p <0.05). Electrical
conductivity did not show a statistical relationship with As. During LF was =
a
high, positive, and significant correlation (p <0.05) observed betw=
een
the As- and pH-level, less strong than during LF (Figure 2). The correlation=
s
between turbidity, color temperature, and electrical conductivity with the
level of As (p >0.05) are not significan=
t
during LF, but significant during HF.
The concentration of As is hig=
her
during HF, because typical in high mountain rivers are sediments and colloid=
al
material transported during intense precipitation events, a process favored
with the increase in pH (COPEA, 2014). Later when the flow decreases are the
particles deposited or when they are co-precipitated with iron oxide. Howeve=
r,
another study (Garc’a et al. , 2011) shows that in the rainy season th=
e
concentration of As in the river water decreases =
due
to dilution and that the concentration of As is higher on the sediments. The=
pH
in rivers ranges between 6.2 and 7.7 and represents oxidized conditions. If
this interval is transferred to the Eh/pH diagram, it shows the zone where
(HAsO4 )2- is predominant present with a high probabili=
ty
to be retained in the solid phase by metallic oxides, clays, etc. As stated =
by
Calvo Revuelta, çlvarez-Bened’, Andrade Ben’tez, Marinero Diez, & Bolado
Rodr’guez (2003) is the concentration of As in ri=
vers
regulated by adsorption-desorption processes responsible for the solubilizat=
ion
or retention of As on sediments. Another study shows that As
dissolves in alkaline river water, confirming the relationship of As
concentration with pH (Richter et al. , 2019). In the present study co=
ntained
the analyzed groundwater samples hardly As, but this might be different in
other aquifers due to the flow regime and mineralogical composition of the
aquifer (Calvo Revuelta et al. , 2019). Risk of As=
contamination in p‡ramos should be avoided at all times, since studies showe=
d
that mining, such as the "Loma Larga" project, leads to an
accumulation of toxic substances in the soil and groundwater, particularly i=
n
periods of low precipitation levels. It is also mentioned that the Kori Koll=
o
p‡ramo (Bolivia) generates for the same reason As
effluents (Pes‡ntez, 2017). Open mining can affect in two ways, namely the
sulfide-based oxidation products that accumulate on the rock surfaces in
combination with heavy rainfall produces Òacid mine runoffÓ and leakage of
alkaline wastewater rich in cyanide, resulting in high concentrations of As (COPEA, 2014). =
p>
=
=
5. &n=
bsp; CONCLUSIONS
The study reveals that
groundwater and p‡ramos in the studied region are free of As, and it is most
appropriate to maintain the conservation state of these ecosystems. The As level in all rivers is tolerable, affected by the
hydrologic regime at the moment of sampling. For example, the As level in the water of the Mach‡ngara and Tarqui rive=
rs is
low during low flow regime, but present in the winter season when the flow
regime of the rivers is high. Arsenic in the surface water comes from
agricultural pesticides and is less likely to be of industrial origin.
Agriculture is the main activity in all studied basins responsible for diffu=
se
pollution, a process difficult to control. The dominant form of arsenic is <=
span
class=3DGramE>As+5 , according to Castro (2004) the least t=
oxic,
possessing a large adsorption capacity on mineral surfaces. The concentratio=
n
of As is pH related, higher in winter, and the pH
favors the As precipitation or desorption from the sediments. The color and
turbidity of the surface water are positively affected by As, and both turn =
out
to be a good indicator of the toxicity of the water, useful tools for the wa=
ter
management boards to decide if the use of the water resource should be limit=
ed.
An increase in the pH enhances the desorption of As
from mineral surfaces, while an increase in the pH promotes the dissolution =
of
iron minerals releasing As. Both these scenarios became clear from mining
(Castro, 2004), and are exaggerated by an increase in the exploitation of
aquifers that modifies the redox potential of the environment. The study has
shown that the analyzed water bodies, with the exception of one station, do =
not
pose a Òcancer riskÓ, and there is also no risk to the ecosystem. However,
under certain conditions the As concentration mig=
ht
reach a worrying level.
=
6. &n=
bsp; RECOMMENDATIONS
The presence of carcinogenic elements in rivers require
permanent monitoring of the water quality. In addition, knowledge of the
hydrogeochemical reactions governed by the redox potential (Eh), the pH, or =
the
presence of other elements is important to establish the contamination risk =
of
As. Furthermore, given the high As concentration =
of
438.8 _g/L found in the Spa of Ba–os, situated in the parish with the same
name, of geochemical origin in combination with the hydrothermal treatment o=
f
the water urges to consider the natural presence of As associated with terti=
ary
and quaternary volcanism in the Cordillera de Los Andes. In addition, to the
analysis of river water samples, it is recommended to also monitor the prese=
nce
of As on the sediments in the rivers. Given the
increasing demand for water and the search for new sources to satisfy the
demand, this study reveals that investigations should include hydrochemical
analyses to guarantee the safe exploitation of the water sources. =
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