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Magnitude of arsenic pollution in the Mekong and Red River
Deltas —Cambodia and Vietnam
Michael Berg
a,
⁎, Caroline Stengel
a
, Pham Thi Kim Trang
b
, Pham Hung Viet
b
,
Mickey L. Sampson
c
, Moniphea Leng
c
, Sopheap Samreth
c
, David Fredericks
d,1
a
Swiss Federal Institute of Aquatic Science and Technology (Eawag), CH-8600 Dubendorf, Switzerland
b
Centre for Environmental Technology and Sustainable Development (CETASD), Hanoi University of Science, Hanoi, Vietnam
c
Resource Development International—Cambodia (RDIC), P.O. Box 494, Phnom Penh, Cambodia
d
Phnom Penh, Cambodia
Received 7 September 2006; accepted 7 September 2006
Available online 1 November 2006
Abstract
Large alluvial deltas of the Mekong River in southern Vietnam and Cambodia and the Red River in northern Vietnam have
groundwaters that are exploited for drinking water by private tube-wells, which are of increasing demand since the mid-1990s. This
paper presents an overview of groundwater arsenic pollution in the Mekong delta: arsenic concentrations ranged from 1–1610 μg/L in
Cambodia (average 217 μg/L) and 1–845 μg/L in southern Vietnam (average 39 μg/L), respectively. It also evaluates the situation in
Red River delta where groundwater arsenic concentrations vary from 1–3050 μg/L (average 159 μg/L). In addition to rural areas, the
drinking water supply of the city of Hanoi has elevated arsenic concentrations. The sediments of 12–40 m deep cores from the Red
River delta contain arsenic levels of 2–33 μg/g (average 7 μg/g, dry weight) and show a remarkable correlation with sediment-bound
iron. In all three areas, the groundwater arsenic pollution seem to be of natural origin and caused by reductive dissolution of arsenic-
bearing iron phases buried in aquifers. The population at risk of chronic arsenic poisoning is estimated to be 10 million in the Red
River delta and 0.5–1 million in the Mekong delta. A subset of hair samples collected in Vietnam and Cambodia from residents
drinking groundwater with arsenic levels N50 μg/L have a significantly higher arsenic content than control groups (b50 μg/L). Few
cases of arsenic related health problems are recognized in the study areas compared to Bangladesh and West Bengal. This difference
probably relates to arsenic contaminated tube-well water only being used substantially over the past 7 to 10 years in Vietnam and
Cambodia. Because symptoms of chronic arsenic poisoning usually take more than 10 years to develop, the number of future arsenic
related ailments in Cambodia and Vietnam is likely to increase. Early mitigation measures should be a high priority.
© 2006 Elsevier B.V. All rights reserved.
Keywords: Arsenic groundwater pollution; Phnom Penh; Hanoi; Health risk; Hair; Urine; Reductive dissolution; Iron; Manganese; Ammonium;
DOC; Kandal province; An Giang province; Dong Thap province; Bassac River
1. Introduction
In some countries, arsenic is the most important
chemical pollutant in groundwater and drinking water.
The Bengal delta region is particularly affected as an
estimated 35 million people have been drinking arsenic-
Science of the Total Environment 372 (2007) 413–425
www.elsevier.com/locate/scitotenv
⁎Corresponding author. Tel.: +41 44 823 50 78; fax: +41 44 823 50
28.
E-mail address: michael.berg@eawag.ch (M. Berg).
1
Present address: 7 Fox Place, Lyneham 2602, Australia.
0048-9697/$ - see front matter © 2006 Elsevier B.V. All rights reserved.
doi:10.1016/j.scitotenv.2006.09.010
rich water for the past 20–30 years (Smedley and
Kinniburgh, 2002). Examination for arsenical dermato-
logic symptoms in 29 thousand people showed that 15%
had skin lesions (Chowdhury et al., 2000). Regions with
arsenic-rich drinking water can be found around the globe
(Smedley and Kinniburgh, 2002). Natural contamination
of groundwater by arsenic is also an emerging issue in
some countries of Southeast Asia, including Vietnam,
Thailand, Cambodia, and Myanmar (Berg et al., 2001;
Buschmann et al., submitted for publication; Polya et al.,
2005). Vulnerable areas for arsenic contamination are
typically young Quaternary deltaic and alluvial sediments
comprising highly reducing aquifers.
Chronic levels of 50 μg arsenic/L can cause health
problems after 10–15 years of exposure (Smith et al.,
2000). The development of symptoms of chronic arsenic
poisoning (arsenicosis) is strongly dependent on expo-
sure time and the resulting accumulation in the body. The
various stages of arsenicosis are characterized by skin
pigmentation, keratosis, skin cancer, effects on the car-
diovascular and nervous system, and increased risk of
lung, kidney and bladder cancer. The European Union
allows a maximum arsenic concentration of 10 μg/L in
drinking water, and the World Health Organisation
(WHO) recommends the same value. In contrast, deve-
loping countries are struggling to establish and imple-
ment measures to reach standards of 50 μg/L in arsenic-
affected areas.
Drinking water supplies in Cambodia and Vietnam are
dependent on groundwater resources (Berg et al., 2001,
2006; Feldmanand Rosenboom, 2001; Fredericks, 2004).
The Mekong and the Red River deltas are the most
productive agricultural regions of South East Asia (see
Fig. 1). Both deltas have young sedimentary deposits of
Holocene and Pleistocene age. The groundwaters are
usually strongly reducing with high concentrations of
iron, manganese, and (in some areas) ammonium. The
Mekong and the Red River deltas are currently exploited
for drinking water supply using installations of various
sizes. In the last 7–10 years a rapidly growing rural
population has stopped using surface water or water from
shallow dug wells because they are prone to contamina-
tion by harmful bacteria. Instead, it has become popular to
pump groundwater using individual private tube-wells,
which is relatively free of pathogens.
The Vietnamese capital Hanoi is situated in the upper
part of the 11,000 km
2
Red River delta, which is inhabited
by 11 million people and is one of the most populous areas
in the world. The exploitation of groundwater in the city
of Hanoi began more than 90 years ago and has since been
expanded several times (Berg et al., 2001). Today, ten
major well-fields are operated by water treatment facili-
ties, which collectively process 650,000 m
3
/day. Due to
naturally anoxic conditions in the aquifers, the ground-
waters contain large amounts of iron and manganese that
are removed in the Hanoi drinking water plants by
aeration and sand filtration (Duong et al., 2003). The
urban water treatment plantsexclusively exploit the lower
aquifers in 30–70 m depth, whereas private tube-wells
predominantly pump groundwater from the upper
aquifers at 12–45 m (Hydrogeological Division II, 2000).
Based on geological analogies to the Ganges delta,
elevated arsenic concentrations in the aquifers of the
Red River basin were expected (Berg et al., 2001). A
first screening by us in 1998 confirmed this assumption
and we studied the extent of arsenic contamination in a
comprehensive survey from 1999 to 2000. The upper
and lower Quaternary aquifers were investigated by
analysing groundwaters from small-scale tube-wells and
pumped by the Hanoi drinking water plants.
Groundwater arsenic contamination was identified in
the Cambodian Mekong delta area in 2000 (Feldman
and Rosenboom, 2001), and has since been investigated
and addressed through close collaboration of local
Fig. 1. Map of Cambodia and Vietnam indicating the Mekong and Red
River deltas. The studied areas are encircled.
414 M. Berg et al. / Science of the Total Environment 372 (2007) 413–425
authorities and NGOs. The first international paper on
arsenic groundwater contamination in Cambodia was
published by Polya et al. (2005).
In this paper, the arsenic levels in groundwater of the
Mekong delta are presented including data for the
Vietnamese delta part, which is reported for the first time.
Inadditiontoanoverviewof the magnitude of arsenic
poisoning in this region, the limited information available
in the international literature on the geology and genesis of
the Mekong and Red River delta is summarised.
2. Materials and methods
2.1. Sample collection
Based on a projected density of one sample per
10 km
2
, private tube-wells were randomly sampled over
areas of 2000 km
2
in Cambodia, 2000 km
2
in Southern
Vietnam, and 700 km
2
in the Red River delta. Ground-
water was collected at the tube by hand or electrical
pumping. Samples were taken after 10 min pumping,
when the oxygen concentration in the water reached a
stable value, which was measured online by using a
dissolved oxygen electrode (PX 3000, Mettler-Toledo).
Redox potential, pH, oxygen levels and conductivity
were recorded on-site. Water was 0.45 μm filtered and
filled in two 500 mL polypropylene bottles. One bottle
for the analysis of metals, ammonium and phosphate
was acidified with approximately 1 mL of concentrated
nitric acid to reach a pH b2. Anions and DOC were
determined in the non-acidified sample. Freshly-drilled
sediment cores were sampled on-site and 20 g wet
sediment filled in polypropylene bags, which were
sealed airtight in the field. Water and sediment samples
were stored at 4 °C in the dark until analysis.
2.2. Chemical analysis
Arsenic concentrations in groundwater samples col-
lected in Cambodia and Southern Vietnam were ana-
lysed in parallel by atomic fluorescence spectroscopy
(AFS) and inductively-coupled-plasma mass spectrom-
etry ICP-MS by the Swiss Federal Institute of Aquatic
Science and Technology (Eawag), as well as by atomic
absorption spectroscopy (AAS) at the Centre for
Environmental Technology and Sustainable Develop-
ment (CETASD). Iron and manganese concentrations
were measured by ICP-MS; ammonium and phosphate
by photometry; nitrate, sulphate and chloride by ion
chromatography; alkalinity by titration; and dissolved
organic carbon (DOC) by a CHN analyser. Ground-
waters from the Red River delta were analysed for total
arsenic at CETASD using AAS. For quality assurance of
these arsenic measurements, 20% of the samples were
sent to Switzerland and analysed by Eawag and an
independent contract laboratory. The results among the
laboratories agreed within 20% deviation.
Sediment samples were freeze-dried, and digested with
concentrated nitric acid and hydrogen peroxide in a
microwave oven. Subsequently, total arsenic was deter-
mined by AFS and metals by ICP-MS. The results obtained
from analysis of sediment digests were confirmed by semi-
quantitative wavelength dispersive X-ray fluorescence
(WD-XRF) carried out at the Swiss Federal Laboratories
for Material Testing and Research. Sediment-bound natural
organic matter was measured with a CHN analyser by
thermal oxidation from groundwater and sediments.
Hair samples of about 2 g were collected from
residents living in villages selected for elevated and low
groundwater arsenic levels. The hair samples were
sealed in polypropylene bags and later tediously washed
in the laboratory by neutral detergent and deionised
water. The hair was digested with concentrated nitric
acid and hydrogen peroxide in a microwave oven (same
as for sediments) and analysed by AAS. Certified refer-
ence material (hair NCSZC 81002) was used to validate
the digestion and analysis procedure. The results from 9
tests (0.58 ± 0.03 mg/kg) were in excellent agreement
with the certified value (0.59 ± 0.07 mg/kg).
3. Results and discussion
3.1. Mekong delta: Cambodia and Southern Vietnam
The Mekong delta is located in southern Vietnam and
neighbouring Cambodia between 8°30′to 11°30′Nand
104°40′to 106°50′E and is confined by the South China
Sea in the southeast, the Gulf of Thailand in the west, the
Vamcodong River in the northeast and a well-defined Late
Pleistocene terrace to the north (Nguyen et al., 2000). The
Mekong River is 4300 km long and has a catchment area
of 520,000 km
2
. It originates in the Tibetan Plateau, and
flows through China, Myanmar, Laos, Thailand, Cambo-
dia and Vietnam. Close to Phnom Penh (Cambodia) the
Mekong divides into two branches, the Mekong to the east
and the Bassac River to the south. The depositional
environment in Phnom Penh is largely limited to a linear
trending valley that is fault controlled along the Bassac
and limited by Pleistocene uplands adjacent to the Mekong.
The Mekong River in Cambodia is a broad, mature river
that becomes tidal upstream to the northeast of Phnom
Penh, near Kampong Cham (Polya et al., 2005). The delta
plain has an area of about 62,000 km
2
, with 10,000 km
2
belonging to Cambodia and the rest located in southern
415M. Berg et al. / Science of the Total Environment 372 (2007) 413–425
Vietnam. The climate is monsoonal humid and tropical,
with average temperatures of 27–30 °C. The rainy season
lasts from April to November (Pham et al., 2002). The
mean annual precipitation ranges from 2400 mm in the
western parts to some 1500 mm in the central and eastern
parts. An estimated 2.4 million Cambodians and 17 million
Vietnamese live on the delta.
The modern delta formed during the last 6–10,000 years
(Holocene) and large areas are tide-dominated areas. The
detailed topography of the delta plain indicates two zonal
parts of the delta (Nguyen et al., 2000). The Holocene
sediment infilled a dissected terrain formed by the 120 m
sea level fall and rise at the end of the Pleistocene. The inner
part is characterized by river-dominated features, while a
well-developed beach ridge system characterizes the outer
part of the delta plain along the coast (Nguyen et al., 2000).
The mean annual water discharge of the Mekong is
15,000 m
3
/s at Phnom Penh and can reach N50,000 m
3
/s in
the rainy season. Great volumes of sediments (160 million
tons/year, mostly composed of silt, clay and sand) are
transported to the South China Sea and the delta consists
almost entirely of young alluvial soils of marine and fluvial
origin (Nguyen et al., 2000). Groundwater varies com-
plexly with depth and is known only in a few areas (Pham
et al., 2002). About 60% of the subaerial delta forms low
flood plains (b2 m above sea-level) with actual or potential
acid sulphate soils (Ollson and Palmgreen, 2001).
3.1.1. Cambodia
3.1.1.1. Reconnaissance studies. The Government of
Cambodia, with support from WHO, conducted a
survey of drinking water quality of water resources
located throughout the country in 2000 (Feldman and
Rosenboom, 2001). The survey, which was conducted
in 13 of Cambodia's most densely populated provinces,
focused on testing the chemical quality of urban and
rural water supplies. A total of 88 groundwater samples
were collected and sent to an Australian laboratory for
the determination of 46 individual pesticides and 21
trace elements including arsenic. Pesticides were very
rarely detected, but 9% of the samples contained arsenic
contents above 10 μg/L. A follow-up study conducted
with 18 groundwater samples originating from the area
where the Bassac River branches off the Mekong (Kien
Svaay and Ta Khman districts, Kandal province) re-
vealed arsenic concentrations of 100–500 μg/L in hand-
pumped tube-wells (Feldman and Rosenboom, 2001).
As a consequence, about 5000 tube-wells were tested
by 25 NGOs in 2002 and 2003 using arsenic field-
testing kits provided by UNICEF (Halperin, 2003).
According to these studies, 20% of the wells located
within risk zones had arsenic levels above 50 μg/L and
50% were above 10 μg/L. A large proportion of these
test-kit measurements were carried-out by RDIC in the
Northern part of the Kandal province, where several
readings exceeded 500 μg/L.
UNICEF, at a water and sanitation donors' meeting
held in Phnom Penh on June 2003 stated that arsenic
concentrations above 50 μg/L have been identified in
Cambodian groundwater (Fredericks, 2004). The
groundwater studies conducted with field test-kits by
UNICEF, RDIC and others in cooperation with Cambo-
dian authorities showed that high concentrations of
arsenic are most often associated with the floodplains of
the Mekong, Bassac, and Tonle Sap Rivers. Arsenic
concentrations in the range of 10–50 μg/L were also
found in unconsolidated sediments along the Mekong
upstream Phnom Penh.
Fredericks (2004) combined this initial data with
geological mapping of unconsolidated sediments to
produce an arsenic risk map for Cambodia presented in
Fig. 2. This map is based on subsurface geology inter-
sected by 17 deep boreholes. The drilling identified
Holocene, Pleistocene, and Plio–Pleistocene sediments
overlying basalt. Groundwater concentrations above
50 μg/L were only identified in young (Holocene)
lowland alluvial deposits. The increased risk of arsenic
polluted groundwater in Holocene alluvial lowland sedi-
ments along the Mekong River and its tributaries was
verified. The floodplains surrounding the Tonle Sap lake
were determined to have low risk in both Pleistocene and
Holocene sediments, and, very low risk in basement
rocks and basalt (Fig. 2). This risk map was largely
confirmed by a survey investigating arsenic levels in
groundwater originating from various parts of Cambodia
(Polya et al., 2005).
3.1.1.2. Own survey of arsenic and other species in
Cambodia groundwater. Between April and December
2004, Eawag and RDI conducted an in-depth groundwa-
ter survey covering the Kandal province and bordering
areas. This province is largely situated on the floodplain
between the Bassac and Mekong Rivers stretching from
Phnom Penh to the Vietnam border in the south (see
Fig. 2). For this study, a set of more than 200 samples was
randomly collected from household tube-wells at a
sampling density of approximately 1 sample per
10 km
2
. Arsenic concentrations ranged from 1–
1610 μg/L (average 217 μg/L, n=207). Arsenic levels
are particularly high in the Kandal province (average
250 μg/L, n=175), while provinces bordering Kandal to
the east and west are much less affected (average 12 μg/L,
n=32). The 14 parameters analysed (see Table 1)indicate
416 M. Berg et al. / Science of the Total Environment 372 (2007) 413–425
that arsenic concentration corresponds to anoxic condi-
tions in the aquifers, leading to reductive dissolution of
arsenic-bearing minerals. These values are comparable to
concentrations reported for Bangladesh and West Bengal
(Smedley and Kinniburgh, 2002; Ahmed et al.,2004; Das
et al., 1996). Bivariate plots of arsenic and selected
parameters are shown in Fig. 3. The correlations of arsenic
with redox potential (Eh), ammonium and DOC are
indicative of reductive dissolution of mineral oxides and
subsequent arsenic release. The trend of higher arsenic
concentrations at pH valuesN7 lead to the speculation that
arsenic release from sediments might partly be enhanced
by alkaline pH, but this needs to be assessed further. A
more in-depth report on this survey has been submitted for
publication (Buschmann et al., submitted for publication).
3.1.2. Southern Vietnam
There is growing concern about the occurrence of
arsenic in groundwater wells of the Vietnamese Mekong
delta. Trang et al. (2005) found elevated arsenic concen-
trations in areas of the Vietnamese Mekong delta, where
40% of the tube-wells had arsenic levels N100 μg/L. The
upper (Quaternary) aquifers of the lower Mekong delta
are typically brackish or saline (Pham et al., 2002). The
soils and aquifers are chemically reducing and contain
natural organic matter of up to 23% in Quaternary depo-
sits (Husson et al., 2000). Groundwater used for public
drinking water supply or irrigation is therefore pumped
from older (Neogene) aquifers at depth of 150–250 m.
According to the Southern Hydrological and Geological
Engineering Department (Ho Chi Minh City), these deep
aquifers should not be affected by elevated dissolved
arsenic concentrations.
Soils rich in iron sulphide (pyrite) are abundant in the
tide-dominated area of the Mekong delta (Husson et al.,
2000). Weathering of the topsoil layer results in the
Table 1
Cambodia: average concentrations and ranges in samples collected
between April and December 2004 (n= 207)
Average Median Range
As μg/L 212 49 b1–1610
Fe mg/L 2.8 1.3 b0.05–16.2
Mn mg/L 0.62 0.39 b0.01–3.3
NH
4
+
mg/L 6.0 2.2 b0.1–52
DOC mg/L 3.9 3.1 b1.3–15.6
HCO
3
−
mg/L 343 337 34–830
NO
3
–N mg/L 0.27 b0.25 b0.25–22
PO
4
–P mg/L 0.59 0.35 b0.2–3.2
Cl
−
mg/L 50 9.0 0.6–1180
Sulphate mg/L 22 b5b5–1020
pH 6.94 6.98 5.42–8.01
Eh mV −65 −69 −410–190
Dissolved O
2
mg/L 1.21 1.10 0.10–4.9
Conductivity μS/cm 752 630 78–6150
Fig. 2. Risk map for arsenic pollution in groundwater of Cambodia (adapted from Fredericks, 2004). Criteria for “increased risk”, low risk”, and “very
low risk”are described in the text.
417M. Berg et al. / Science of the Total Environment 372 (2007) 413–425
oxidation of these sulphides, leading to large amounts of
sulphuric acid. The resulting acidic conditions can cause
pH-values below 3 (Husson et al., 2000). Consequent
acidification of the canals and the rivers make the water
unsuitable for irrigation and drinking. Oxidation of
pyrite results mostly from lowering of the water table
(Minh et al., 1998). Gustafsson and Tin (1994) analysed
25 such acid sulphate soils from the Mekong delta. The
arsenic contents ranged from 6 to 41 μg/g and were
classified ‘elevated’by global average values.
The high amount of rainfall during the rainy season
combined with high river flow lead to annual flooding of
the area. However, in the dry season the levels of the rivers
drop significantly due to excessive irrigation demands,
which are leading to increased inland flow of seawater
through the Mekong and Bassac River channels.
Much of the rural population has limited access to
safe drinking water. Tube-wells are therefore installed
wherever possible and affordable. With increasing dis-
tance from the sea, the groundwater salinity in shallow
aquifers decreases, so that the groundwater becomes a
suitable source of drinking water that can easily be
pumped through small-scale tube-wells. The recognition
of arsenic pollution in the Cambodian part of the
Mekong delta (see above) strongly suggests that the
Vietnamese delta region is also affected. Hence, we have
conducted a groundwater survey in the upper part of the
Vietnamese Mekong delta where shallow aquifers are
not considered saline. This area belongs to the same
geological unit as the strongly arsenic affected Kandal
province of Cambodia.
3.1.2.1. Concentrations of arsenic and other species in
groundwater of Southern Vietnam. In Vietnam, the
Bassac and Mekong Rivers (sometimes called Tien Giang
and Hau Giang Rivers in Vietnam) flow through the An
Giang and Dong Thap provinces before fading-out in the
Mekong delta flood plain. Our study focused on these two
provinces (see Fig. 1) since the Holocene aquifers of this
region are generally unaffected by salt water intrusion. A
Fig. 3. Bivariate plots of arsenic and selected parameters measured in groundwater samples of the upper Mekong Delta, Cambodia and Vietnam.
Open circles (○) are samples from Cambodia (n= 207), black dots- (•) from southern Vietnam (n= 112). a) redox potential–arsenic, b) pH–arsenic,
c) ammonium–arsenic, d) dissolved organic carbon–arsenic.
418 M. Berg et al. / Science of the Total Environment 372 (2007) 413–425
large portion of the people still use surface water for their
daily needs including drinking water. But family-based
tube-wells are used increasingly as an alternative.
On July 2004, we randomly collected 112 ground-
water samples in this rural area (Trang et al., 2005).
Table 2 provides an overview of average concentrations
and ranges of parameters measured in this study. Arsenic
ranged from b1–845 μg/L (average 39 μg/L). Concen-
tration ranges of other parameters are listed in Table 2.
The magnitude of Fe, ammonium, and DOC concentra-
tion are similar as the ones in the upstream Kandal
province of Cambodia (see Table 1 and Fig. 3).
Although arsenic concentrations reach levels
N500 μg/ L, the average is significantly lower than in
Cambodia. The chemical groundwater composition sum-
marised in Table 2 and plotted in Fig. 3 further reveals that
dissolved manganese and chloride are more abundant.
Elevated arsenic levels are often found in samples with pH
valuesN7 where arsenic release from sediments might be
enhanced, but the major cause for arsenic pollution seems
primarily related to reductive dissolution.
Arsenic concentrations averaged at 64 μg/L within a
distance of b10 km from the rivers, while samples in the
farther distance (N10 km) had a much lover average of
8μg/L. This trend is consistent with the finding for
Cambodia where the most severe arsenic pollution is found
in tube-wells located in the alluvial flood-plain between the
Bassac and Mekong Rivers (Kandal province).
3.2. Red River delta, Northern Vietnam
The Red River basin stretches from N 20°00′to N
25°30′and E 100°00′to E 107°10′and is confined by
the Truong Giang and Chau Giang River basins in the
north, the Mekong in the west, the Ma River basin in the
south and the Gulf of Tonkin in the east. The Red River
has a total length of 1150 km and its basin has a catch-
ment area of 170,000 km
2
. It is dominated by tropical
monsoon climate and is subject to rainy seasons (May–
September) and dry seasons (October–April). The
average temperature in Hanoi is 23.4 °C and the average
rainfall is 1800 mm/year. During the rainy season, the
Red River in Hanoi may reach a water discharge of
9500 m
3
/s; the long-term average flow is 3740 m
3
/s, but
the river volume is highly variable throughout the year.
The Red River delta is a flat area with a ground level
of 5 to 8 m above mean sea level. It has a complicated
geological history with up-and-down movements, trans-
gressions, erosion and stream activities that formed the
alluvial sediments. The result of these geological
processes is a relatively thick Quaternary accumulation
(50–90 m in Hanoi) with loose and altering sediment
beds, many containing organic material. In general, the
Quaternary can be divided into two sequences: the upper
part, composed of fine sediment clay, sandy clay and
fine sand; and the lower part, containing gravel with
cobbles and coarse sand. The Quaternary sediments are
underlain by Neogene sedimentary rocks that are com-
posed of conglomerate sandstone, clay and siltstone. In
total the Neogene exceed a thickness of 400 m. More
detailed information can be found in Berg et al. (2001)
and references therein.
A tentative risk map of arsenic being N50 μg/L in
groundwater of the Red River delta is presented in Fig. 4.
This map was established from geological raster infor-
mation, climate and land use (geo-referenced raster data
was obtained from FAO, www.fao.org/geonetwork).
Correlation with measured arsenic values in groundwater
was best for recent alluvial sediments of loamy texture
(high risk), other Holocene sediments (medium risk) and
Pleistocene sediments (low risk). It must be noted that the
coastal areas (some 25 km wide) have saline groundwater,
which is not used for drinking.
3.2.1. Arsenic pollution in tube-wells of rural areas
(upper aquifer)
Fig. 5 shows arsenic concentrations measured in the
rural districts on December 1999. The concentrations
varied greatly within the studied area, but most tube-
wells yielded arsenic concentrations above the WHO
guideline of 10 μg/L. In the southern part (district D),
most arsenic concentrations exceeded the Vietnamese
standard of 50 μg/L.
Our ongoing investigations reveal that the variability
of arsenic levels is very pronounced, even within dis-
tances of 10–20 m. This is illustrated in Fig. 6 which
Table 2
Vietnamese Mekong delta: average concentrations and ranges in
samples collected on July 2004 (n= 112)
Average Median Range
As μg/L 39 b1b1–845
Fe mg/L 2.6 b0.05 b0.05–56
Mn mg/L 3.4 0.97 b0.01–34
NH4
+
mg/L 5.0 1.4 b0.1–35
DOC mg/L 5.3 2.6 1.5–58
HCO3
−
mg/L 230 190 19–785
NO3–N mg/L b0.25 b0.25 b0.25–4.4
PO4–P mg/L 0.33 b0.2 b0.2–5.25
Cl
−
mg/L 690 374 2.1–8570
Sulphate mg/L 41 15 b5–360
pH 6.83 6.80 5.00–8.70
Eh mV 14 24 −303–625
Dissolved O
2
mg/L 0.29 0.20 b0.01–3.90
Conductivity μS/cm 2490 1710 224–17900
419M. Berg et al. / Science of the Total Environment 372 (2007) 413–425
shows high variations of arsenic concentrations in a
small village located in district D.
3.2.2. Public drinking water supply of the city of Hanoi
(lower aquifer)
Raw water (lower aquifer) and treated water from the
eight groundwater treatment plants of Hanoi were sampled
and analysed seven times between March 1999 and July
2000. The concentrations of December 1999 showed that
some raw groundwaters contained greater than 300 μg/L
arsenic (Berg et al., 2001). Although arsenic concentrations
were substantially lowered by treatment, the levels in
finished waters (25–91 μg/L) still exceeded the Vietnamese
limit in half of the samples (Dodd et al., 2006). However,
most tap-water samples collected at individual homes
contained arsenic concentrations below 50 μg/L (range
7–82 μg/L, average 31 μg/L), suggesting that additional
arsenic removal occurs in the distribution system, possibly
by adsorption to iron oxide surfaces in the pipes of the
distribution system (Berg et al., 2001).
3.2.3. Origin of arsenic pollution
Although there is no indication for an anthropogenic
origin of arsenic in the subsurface in and around Hanoi, the
possibility of pollution through landfill leakage, agricul-
tural fertilizers (McLaughlin et al., 1996)orminingwastes
carried by the Red River cannot be excluded. However, the
widespread occurrence of arsenic in the investigated
aquifers points to natural geogenic sources similar to the
situation in the Ganges delta (BGS and DPHE 2001; Das
et al., 1996; McArthur et al., 2001; Nickson et al., 2000).
Sediment-bound arsenic most probably originates from
erosion and weathering processes, which result in the
Fig. 4. Tentative risk map for arsenic being N50 μg/L in groundwater
of the Red River delta, Vietnam. The criteria for “low risk”,“medium
risk”, and “high risk”are described in the text.
Fig. 5. Arsenic concentrations measured in groundwaters of the larger Hanoi area in samples pumped from the upper aquifer by private tube-wells (December
1999).
420 M. Berg et al. / Science of the Total Environment 372 (2007) 413–425
enrichment of arsenic onto ferric oxyhydroxides followed
by fluvial transport and sedimentation (Rodwell, 1994;
Welch et al., 1988). Several studies (BGS and DPHE 2001;
Korte and Fernando, 1991; McArthur et al., 2001; Nickson
et al., 2000) have suggested that elevated arsenic levels in
groundwater are caused by reductive dissolution of arsenic-
rich iron oxyhydroxides occurring as dispersed phases in
the aquifer rocks.
The anoxic conditions in the Red River sediments are
driven by natural organic matter (NOM) present in the
subsurface (Berg et al., 2001; Trafford et al., 1996): we
have found peat layers with NOM concentrations of
15% total organic carbon in sediment cores. Dissolved
oxygen is rapidly consumed by microbiological miner-
alization of NOM, resulting in the formation of bicar-
bonate and inorganic nitrogen species. This is consistent
with the high alkalinity (up to 810 mg/L) and high
nitrogen concentrations (10–48 mg N/L) measured in
the studied groundwaters. Inorganic nitrogen was
mainly found in the reduced form of ammonium that
reached particularly high levels of up to 48 mg N/L in
the most severely arsenic-contaminated district D (Berg
et al., 2001). As a result of the low redox potential, As
(V) is reduced to As(III) which contributes 50–100% of
total arsenic in the groundwaters.
In order to explain the significantly different arsenic
levels of districts A and D (Fig. 5), the different geological
settings and actual hydrogeological conditions of these
areas must be considered. The geology of the Red River
delta is complex, with considerable variation in lithology
within short distances. The sediments in district A
(predominantly of Pleistocene age) are not as thick as
those in the other districts, and form mainly one aquifer 10–
25 m in depth. The other districts have sediment layers from
both the Pleistocene and Holocene ages, with the latter
being partly derived from postglacial marine transgressions
(Trafford et al., 1996). Of the 2–3 present aquifers, the first
(10–30 m) and the second (30–70 m) are exploited for
drinking water. Due to frequent riverbed migrations, the
aquifers are not fully separated and are in some locations
connected through sand lenses. Even without the pumping
of groundwater, recharge in the upper two (Quaternary)
aquifers can partly originate from Red River bank
filtration. However, Hanoi's high demand of water is
causing a significant drawdown of the groundwater table.
This is particularly severe in districts B and D where cones
of depression reach 30 m deep. Under these conditions,
bank filtrates from the Red River must be of major
importance and strongly influence the groundwater
recharge in the Hanoi area. More detailed information
can be found in Berg et al. (2001) and references therein.
3.2.4. Sediment arsenic concentrations
Total arsenic concentrations vary with depth in
stratigraphically different sediment layers of five
sediment cores (12–40 m depth, mainly upper aquifer).
The locations of the sediment drilling sites are marked in
Fig. 5 and concentration depth profiles are shown in
Fig. 7. The cores were drilled next to groundwater
monitoring wells, and water of these wells was sampled
concurrently. In the upper 10 m of two cores, distinct
peat layers were present. Peak arsenic concentrations
Fig. 6. High variations of arsenic levels are observed over short distances. As an example, this map shows As groundwater concentrations measured
on March 2001 in a village. The numbers indicate As concentrations in μg/L.
421M. Berg et al. / Science of the Total Environment 372 (2007) 413–425
of 6–33 μg/g were primarily associated with brown
to black–brownclaylayers,followedbygreyclay
(2–12 μg/g) and brown-to-grey sand (0.6–5μg/g). The
arsenic content was highly correlated with the iron
content, indicating that arsenic could be adsorbed with
iron phases (Fig. 7). No correlation was observed for
sediment-bound arsenic with dissolved arsenic concen-
trations measured in groundwater of the adjacent
monitoring wells.
3.2.5. People at risk of chronic arsenic poisoning
The results of this survey reveal that several million
people of the Red River delta are exposed to a risk of
chronic arsenic poisoning. Yet, to the best of our knowl-
edge, only few disease symptoms have been diagnosed
so far. This could possibly be attributed to the fact that in
Vietnam, arsenic contaminated groundwater has only
been used as drinking water for the past 7–10 years.
Furthermore, the early manifestations of arsenicosis are
difficult to diagnose and depend largely on the aware-
ness of the local doctors (Saha et al., 1999). The fre-
quencies of the concentration ranges reveal that 25–
90% (average = 48%, n= 196) or 50–98% (aver-
age = 72%, n= 196) of the investigated groundwaters
exceed the arsenic limit of 50 μg/L or 10 μg/L, res-
pectively. This means that the Hanoi area and possibly
larger areas of the Red River delta are as strongly
affected as Bangladesh (27% above 50 μg/L, n= 3534)
(BGS and DPHE, 2001). The very high concentrations
in district D raise the question why no arsenicosis has
been detected to date. Experience shows that it can take
ten or more years before the first arsenic poisoning
symptoms to become apparent. Compared to Bangla-
desh, one might further speculate that the general nutri-
tion of the Vietnamese population is better and that this
could have a retarding influence on the manifestation of
the disease. Hence, the number of people affected in the
future by arsenic-related health problems should not be
underestimated.
3.3. Indicators for human arsenic exposure
3.3.1. Cambodia (Mekong delta)
Arsenic concentrations were measured in some 20
hair and urine samples from residents of a farming
village exposed to high groundwater As levels. These
values were compared with control sites (Agusa et al.,
2002). Arsenic levels found in human hair at the
exposed village (average 2.0 mg/kg) were significantly
higher ( p= 0.05) than at the control site (average 0.3 mg/
kg). On the other hand, no regional difference in urinary
As concentrations (median values 53–81 μg/L) was
observed. However, in this study the highest As con-
centration in urine (490 μg/L) was detected in the
sample of a resident living in the As-contaminated area.
At this concentration, symptoms of arsenicosis can be
expected to develop (Fredericks, 2004). As depicted in
Fig. 8a, the exposure to high arsenic concentrations of
people living in the Kandal province is clearly reflected
in the hair arsenic levels reported by Agusa et al. (2002).
Like in Vietnam, most of Cambodia's 40,000 tube-
wells were built in the past decade (Kyne, 2000),
indicating that serious As related health problems might
not yet have emerged. Nevertheless, cases of skin prob-
lems in children that may be traceable to As have been
identified in a few cases (Sine, 2002).
Fig. 7. Vertical depth profiles of sediment-bound total arsenic and total iron depicted for three of the five sediment cores drilled on July 2000. Notes:
grey background indicates confining sediment layers (e.g. clay and silt). The layers of the white area consisted mainly of sand and gravel.
422 M. Berg et al. / Science of the Total Environment 372 (2007) 413–425
3.3.2. Southern Vietnam (Mekong Delta)
The As exposure of people living in the Vietnamese
part of the Mekong delta was investigated in a survey
conducted in 2004 (Trang et al., 2005). Hair samples
were randomly collected in two villages, one being
exposed to groundwater arsenic pollution and the other
having arsenic levels b50 μg/L. These hair samples
were analysed together with groundwater sampled
from tube-wells, from which these people are pumping
drinking water. The As levels found in hair ranged from
0.11–2.92 mg/kg and from 1–167 μg/L in groundwater.
As can be seen in Fig. 8b, remarkably higher As
concentrations were measured in hair from people living
in the village exposed to arsenic groundwater pollution
than in the control village using safe water. The dif-
ference of the two groups is statistically significant with
p-values b0.001 for both, hair and groundwater. No
conclusions regarding health symptoms can be inferred
from these findings, however, they clearly indicate that
people of the upper Mekong River delta are chronically
exposed to elevated As levels in their drinking water.
3.3.3. Red River delta
In 2001 we have examined the human arsenic
exposure in the Red River delta. Hair probes from 51
randomly selected residents were sampled in rural areas
and the arsenic levels compared with groundwater
collected from their tube-wells. The As concentrations
ranged from 0.20–2.75 mg/kg in hair and from
1–310 μg/L in groundwater. Arsenic in hair of people
drinking groundwater with arsenic levels N50 μg/L were
evidently higher than of people belonging to the group
b50 μg/L (see Fig. 8c). The difference of the two groups
Table 3
Arsenic concentrations (μg/L) in groundwaters of rural districts (upper
aquifer, Red River delta)
District
a
n
b
Average Range
A48321–220
B48671–230
C 55 140 2–3050
D 45 430 2–3010
All districts 196 159 1–3050
Notes: three sample series: September 1999, December 1999, May
2000. (a) Districts A to D are as shown in Fig. 7. (b) number of
analysed samples.
Fig. 8. Box plots of arsenic concentrations in groundwater and hair of
residents living in rural areas. a) Kandal province and bordering
provinces in Cambodia. b) Upper Vietnamese Mekong delta. c) Red
River delta, Vietnam. Average values are indicated by solid lines (—),
medians by dashed lines (- - -). The columns contain 50% of the data,
the vertical lines 95%. Open circles are data points outside the 95%
range. The p-values are derived from a paired t-test.
423M. Berg et al. / Science of the Total Environment 372 (2007) 413–425
is statistically significant with p-values of b0.001 for
both, hair and groundwater. This data is demonstrating
that people of the Red River delta are chronically
exposed to elevated arsenic levels in their drinking water
(Tab le 3). Similar arsenic concentrations found in
human hair (0.09–2.8 mg/kg) of people living in the
rural Hanoi area were reported by Agusa et al. (2002).
4. Conclusions and outlook
Based on the data presented here, arsenic ground-
water pollution in Cambodia and Vietnam is evident and
its impact to humans clearly reflected in the high arsenic
levels measured in hair of people consuming such
groundwater. We currently estimate that 10 million
people in the Red River delta and 0.5–1 million people
in the Mekong delta are at risk of chronic arsenic
poisoning. Considering the magnitude of arsenic pol-
lution, early mitigation measures are urgently needed to
protect the people from serious health problems.
Household sand filters capable of removing in average
80% arsenic have recently been shown to be particularly
efficient and socially accepted in the Red River delta
(Berg et al., 2006; Luzi et al., 2004). Options for arsenic
removal have also been suggested for communal supply
water (Pham et al., 2003; Dodd et al., 2006). Investiga-
tions on the occurrence and magnitude of As contam-
ination in Vietnamese groundwaters have so far focused
on the Red River delta of northern Vietnam (Berg et al.,
2001) and the Mekong delta in the south (Trang et al.,
2005). However, other potential areas for As-rich
groundwater including the Ma, Ca, Gianh, Huong, and
Da Rang river deltas have not yet been assessed.
Likewise, besides the Kandal province and neighbour-
ing areas, there is an urgent need to investigate further
regions in Cambodia as indicated in the risk map
presented in Fig. 2. Obviously the extent of the arsenic
problem must more closely be assessed in Cambodia
and Vietnam.
Acknowledgements
We thank for the financial support by the Swiss
Agency for Development and Cooperation. We acknowl-
edge Nguyen Van Dan, Tong Ngoc Thanh, Nguyen van
Hung, Nguyen Kim Quyen and Nguyen Trac Viet for
fruitful discussions and for providing hydrological
information. We are very grateful to Mengieng Ung,
Kagna Ouch, Sovathana Vong and Rachna Oum for
assisting in the sampling campaigns in Cambodia; to Vu
Van Trinh, Phan Van Han for assisting in the sampling
campaigns in the Vietnamese Mekong delta; to Vi Mai
Lan and Bui Hong Nhat, Nguyen Minh Hue, Pham Thi
Dau, Tran Thi Hao for assisting in the sampling
campaigns in the Red River delta; to Jakov Bolotin and
David Kistler for analytical measurements; and to
Johanna Buschmann for artwork of Fig. 3.The
information and reports provided by Chander Badloe,
Waldemar Pickardt, Steven Iddings, and Peter Feldman
are acknowledged.
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