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CHARACTERIZATION OF ACCUMULATED
SEDIMENTS IN BIO-REMEDIATION
CHAMBERS AT ESTERO DE BALETE
Banta, Mhadel A.
Candelaria, Camille G.
Pagasartonga, Mon Eric P.
Ricarte, Shienah C.
CHEMICAL ENGINEERING
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Adamson University
College of Engineering
Chemical Engineering Department
A Research Study Presented to
The Faculty of Chemical Engineering Department
In Partial Fulfillment of the
Requirements for the Degree of
Bachelor of Science in Chemical Engineering
CHARACTERIZATION OF ACCUMULATED SEDIMENTS IN
BIO-REMEDIATION CHAMBERS AT ESTERO DE BALETE
Banta, Mhadel A.
Candelaria, Camille G.
Pagasartonga, Mon Eric P.
Ricarte, Shienah C.
APRIL 2011
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APPROVAL SHEET
This research entitled:
“Characterization of Accumulated Sediments in Bio-Remediation Chambers at
Estero De Balete”
Prepared and submitted by:
Banta, Mhadel A. Candelaria, Camille G,
Pagasartonga, Mon Eric P. Ricarte, Shienah C.
Engr. Jerry G. Olay
Adviser
Has been successfully defended last March 29, 2011 and was approved last April 12,
2011.
Engr. Sherrie Mae S. Medez
Panelist
Engr. Merlinda A. Palencia
Chairperson
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DECLARATION
This research study hereto is entitled:
“Characterization of Accumulated Sediments in Bio-Remediation Chambers at
Estero De Balete”
This report is a summary of our findings from the work we completed this 2nd
semester
of 2011 and is submitted as an output for compliance with the requirements leading to
the Degree of Bachelor of Science in Chemical Engineering.
Prepared and submitted by:
Banta, Mhadel A. Candelaria, Camille G,
Pagasartonga, Mon Eric P. Ricarte, Shienah C.
Engr. Merlinda Palencia
Chairperson
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ACKNOWLEDGEMENT
We would like to dedicate this study first of all to God Almighty, He who
helped and guided us all throughout our experiment.
We would like also to take the opportunity to acknowledge Engr. Palencia for
allowing us to be part of her study. It is our honor to take part in behalf of Adamson
University ChE Student Research for the rehabilitation of Estero De Balete. Our
adviser, Engr. Olay, for giving us his time unconditionally. Engr. Evangelista, for
being patient with us at the ChE Laboratory.
Allow us also to give token of appreciation to our fellow classmates by citing
them here. We thank all of you classmates, batch mates and friends. We also
acknowledge our family by supporting us regardless our misgiving.
In behalf of our Research Group, we hope that this study can be a reliable
guide in rehabilitating the Estero de Balete.
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Table of Contents
Abstract i
List of Figures and Tables iii
1 Introduction 1
1.1 Background of Study 1
1.2 Statement of the Study 2
1.3 Significance of the Study 3
1.4 Scope and Delimitation of the Study 3
1.5 Theoretical Framework 4
1.6 Conceptual Framework 6
1.7 Definition of Terms 7
2 Review of Related Literature and Studies 9
2.1 Related Literature 9
2.1.1 Sediments 9
2.1.2 Effects of Heavy Metal Contamination in Human Health and the
Environment 11
2.1.3 Sediments Quality Guidelines 15
2.1.4 Bioremediation 20
2.1.5 Total Organic Carbon 21
2.1.6 Total Phosphorus 22
2.1.7 Total Kjeldahl Nitrogen 24
2.1.8 Equipment 25
2.2 Related Studies 26
3 Methodology 31
3.1 Description of Study Area 31
3.2 Preparation of Sampling Bed and Containers 32
3.3 Selection of Sampling Site 33
3.4 Collection of Sediment Samples 33
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4 Data Presentation, Analysis and Interpretation of Results 35
4.1 Physical Properties of Collected Sediments 35
4.2 Heavy Metal Concentration of Collected Sediments 36
4.3 Nutrient Content of Collected Sediments 37
4.4 Assessment of Collected Sediments using Sediment Quality
Guidelines 38
4.4.1 Ontario Ministry Sediment Quality Guideline 38
4.4.2 Hong Kong Sediment Quality Guideline 44
4.5 Accumulation Rate of Sediments 47
5 Summary of Findings, Conclusions and Recommendations 48
5.1 Summary of Findings 48
5.2 Conclusions 49
5.3 Recommendations 50
Appendices 51
Appendix A: Results of Analyses 51
Appendix B: Calculation of Accumulation Rate of Sediments 53
Appendix C: Research Images 55
Appendix D: References 60
Resume of Researchers 63
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Abstract
Estero de Balete is one of the tributaries of Pasig River that have been
contaminated because of accumulation of wastes and refuse which are hazardous in
nature. In this study, a Bioremediation test was done on Estero de Balete and the
physical and chemical properties of accumulated sediments were determined. Also,
determination of heavy metal content (Copper, Lead, Cadmium and Mercury) of
sediments was also part of this study.
The remediation technique was conducted for about 2 months. Two runs were
done but the analysis for the second run was used in this report because more
significant change in the contaminants was observed. The concentrations of the heavy
metals were measured using Flame Atomic Absorption Spectrophotometer (AAS)
while the nutrient contents (Total Kjeldahl Nitrogen, Total Phosphorus and Total
Organic Carbon) of sediments were determined using Kjeldahl Method, Stannous
Chloride Method and Ascorbic Acid Method.
In the Philippines, there are currently no Sediment Quality standards and the
most commonly used guidelines are from Ontario Sediment Quality Guidelines and
National Oceanic Atmospheric Administration (NOAA). For this study, we have
compared the attained sediment analysis with Ontario Sediment Quality Guidelines
and Hong Kong Sediment Quality Guidelines to determine if the collected sediments
would have any adverse effect to the environment. Results showed that, after the
remediation, the contaminants pose no serious effect to the environment.
The analysis in this study could be of great help in finding ways to decrease the
contamination of these hazardous substances in Rivers and in its tributaries that induce
harmful effects to the environment and human help. This study can also be used as
technical references in the rehabilitation of Pasig River.
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List of Figures and Tables
Figure 1 Experimental Procedure
Figure 3.1a Bioremediation Chambers
Figure 3.1b Experimental Design for the Determination of Accumulation Rate
Figure 3.2 Sampling Bed
Figure 3.3 Sampling Points for Determination of Accumulation Rate
Figure 4.2 Graphical Representation of Heavy Metal Concentrations of Collected
Sediments
Figure 4.3 Graphical Representation of Nutrient Concentrations of Collected
Sediments
Figure 4.4a Comparison of Copper Concentration from the Collected Sediments with
Ontario Sediment Quality Guidelines
Figure 4.4b Comparison of Lead Concentration from the Collected Sediments with
Ontario Sediment Quality Guidelines
Figure 4.4c Comparison of Cadmium Concentration from the Collected Sediments
with Ontario Sediment Quality Guidelines
Figure 4.4d Comparison of Mercury Concentration from the Collected Sediments
with Ontario Sediment Quality Guidelines
Figure 4.4e Comparison of Total Kjeldahl Nitrogen Concentration from the
Collected Sediments with Ontario Sediment Quality Guidelines
Figure 4.4f Comparison of Total Phosphorus Concentration from the Collected
Sediments with Ontario Sediment Quality Guidelines
Figure 4.4g Comparison of Total Organic Carbon Concentration from the Collected
Sediments with Ontario Sediment Quality Guidelines
Figure 4.4h Comparison of Copper Concentration from the Collected Sediments with
Hong Kong Sediment Quality Guideline
Figure 4.4i Comparison of Lead Concentration from the Collected Sediments with
Hong Kong Sediment Quality Guideline
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Figure 4.4j Comparison of Mercury Concentration from the Collected Sediments
with Hong Kong Sediment Quality Guideline
Table 2.1 Ontario Ministry of Screening Level Guidelines
Table 3.4 Methods Used for the Analysis of Total Phosphorus, Total Organic
Carbon, Total Nitrogen and Heavy Metals
Table 4.1 Physical Properties of Collected Sediments
Table 2.2 Ontario Sediment Quality Benchmarks
Table 2.3 Sediment quality guideline values Lower Concentration Exceedance
Level (LCEL) and Upper Concentration Exceedance Level (UCEL) of
Hong Kong
Table 4.5 Accumulation Rate of Sediments in each Filter Bed per Unit Area
Table 5.1 Concentrations of Lead, Mercury, Copper, Cadmium and Nutrients from
Sediments Collected after the Bioremediation Treatment and from Sediment Quality
Guidelines (ppm)
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CHAPTER 1
INTRODUCTION
1.1 Background of Study
Sediments are loose particles of clay, silt and other substances that settle at the
bottom of water body. Sediments play an important role in aquatic ecosystem since
they serve as a source and sink for organic and inorganic materials and as habitat for
many organisms in aquatic food webs. The series of sediment-induced changes that
can occur in a water body may change the composition of an aquatic community
(Wilber, 1983). Nowadays, many of these sediments in our lakes, rivers, oceans and
other bodies of water have been contaminated by pollutants, which enter our bodies of
water. Experts believed that contaminated sediments are a wide spread and serious
problem. Recent studies revealed that the true state of the quality of water is reflected
by the quality of its underlying sediments.
The Pasig River one of the major Rivers in the Philippines serves as a major
transport route, source of water and life line of Laguna de Bay and irreplaceable
natural resources. Yet, for centuries Pasig River has been used, abused and neglected
and not the River has been declares a critical water body because of the unspeakable
amount of waste dumped into it by daily household and industries. About 330 tons of
industrial and domestic wastes are discharge every day in this water way, depleting the
biochemical oxygen needed to support marine life. (Menchit R. Santelices)
Until recently, little has been done to protect the river system. Past efforts to
rehabilitate Pasig River were unsuccessful because they failed to take into account the
larger context of the urban environment of which Pasig River is apart.
Recently, Adamson University, together with Chemical Engineering
department, established “Bio-remediation Techniques for Rehabilitation of Estero de
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Balete” which aims to revive and rehabilitate the water and sediments of Estero de
Balete through the application of natural minerals available in the Philippines. The
information on the effects of locally available natural materials on the treatment of
Estero water and sediments will provide concrete technical and methodical basis to
rehabilitate Pasig River into a more stable ecosystem.
1.2 Statement of the Study
This study aims to determine the characteristic of sediments that settled from
the treated water in the bioremediation chambers at Estero de Balete. Specifically, the
study aims to:
1. Determine the physical and chemical characteristic of the sediments of
Estero de Balete in terms of the following parameters:
1.1 Physical properties
1.1.1 Color
1.1.2 Odor
1.2 Chemical properties
1.2.1 Total Phosphorus
1.2.2 Total Kjeldahl Nitrogen
1.2.3 Total Organic Carbon
2. Measure the concentration of cadmium, copper, mercury and lead the
sediments
3. Evaluate the extent of heavy metal and nutrients, i.e. Total Phosphorus,
Total Kjeldahl Nitrogen and Total Organic Carbon, of sediments in terms
of the following guidelines:
3.1 Ontario Sediment Quality Guidelines
3.2 Hong Kong Sediment Quality Guideline
4. Determine the daily sludge formation/ accumulation rate
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1.3 Significance of the Study
The physical and chemical characterizations of accumulated sediments in
bioremediation chamber are the primary concern of the study. Through this research,
the Adamson community and people living along the Estero would be aware of the
possible problem regarding contamination of sediments, this enable us to focus our
efforts on activities that achieve the best environmental results. Finally, the
characteristic of sediments gathered may help establish an effective bioremediation
treatment for Estero de Balete.
1.4 Scope and Delimitation of the Study
The study focused on the characterization of the physical and chemical
properties of sediments on the bioremediation chamber at Estero de Balete.
Sediment sampling was done only after the removal of treated water in the
chamber. There are two chambers and only three sites of the chamber are to be
considered. The heavy metals determined were cadmium (Cd), copper (Cu), mercury
(Hg) and lead (Pb).The comparison of the level of heavy metal contamination of
sediments with environmental protection agency (EPA) level of hazardous chemicals
focused on the four metals mention above and also comparing the results with the
established heavy metal concentration of sediments found in Estero de Balete.
Determination of total nitrogen and phosphorus and total organic carbon is also
considered. Biological characteristic of sediments such as soil form organism, specific
microorganism and total toxicity are not assessed. Under the physical characteristics of
sediments the following are determined: color and odor. The study will also determine
the daily sludge formation or accumulation rate per unit area.
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1.5 Theoretical Framework
Many of the sediments in our rivers, lakes, and oceans have been contaminated
by pollutants. Some of these pollutants, such as the pesticide and the industrial
chemicals, were released into the environment long ago. Other contaminants enter our
waters every day. Some flow directly from industrial and municipal waste dischargers,
while others come from polluted runoff in urban and agricultural areas. Still other
contaminants are carried through the air, landing in lakes and streams far from the
factories and other facilities that produced them.
Heavy metals are one of the most persistent pollutants in water. Unlike other
pollutants, they are difficult to degrade, but can accumulate throughout the food chain,
producing potential human health risks and ecological disturbances. Their presence in
water is due to discharges from residential dwellings, groundwater infiltration and
industrial discharges. The discharge of wastewater containing high concentrations of
heavy metals to receiving water bodies has serious adverse environmental effects.
Their occurrence and accumulation in the environment is a result of direct or indirect
human activities, such as rapid industrialization, urbanization and anthropogenic
sources (EPA, 2000; Hussein et al., 2005; Gardea-Torresdey et al., 2005; Martin-
Gonzalez et al., 2006).
A small amount of contamination of heavy metal to our bodies of water may
lead to serious environmental problem. Heavy metals can either be absorbed by the
sediments or accumulated by benthic organism to toxic levels; the bioavailability and
subsequent toxicity of the metals are dependent upon the various forms and amount of
the metal bound to the sediments.
Sediment quality is determined according to its effect on water quality and
aquatic life. The No Effect Level (NEL) has zero effect on the aquatic living
organisms. The Low Effect Level (LEL) is the Level in which there is little effect on
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the sediment–dwelling organisms. At the Severe Effect Level (SEL) affects the health
of the sediment-dwelling organisms and is considered to be heavily polluted.
Also, sediment quality is also determined based on its level of toxicity. The
lower chemical exceedance level (LCEL) represents a value below which
contaminants in the sediment are not expected to have adverse biological effects,
whereas the upper chemical exceedance level (UCEL) represents a value above which
toxicity is likely.
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1.6 Conceptual Framework
Figure 1 Experimental Procedure
Collection of
samples
Preparation of
containers
Laboratory analysis
Heavy Metal
Analysis
(Cd, Cu, Hg and Pb)
Physical
Properties
Chemical
Properties
Color
Odor
Total
Phosphorus
Content
Total Organic
Carbon Content
Interpretation of
Data
Drawing of
Conclusion
Total Nitrogen
Content
Preparation of
sampling bed
Collection of
samples
Accumulation Rate
Determination
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1.7 Definition of Terms
1. Bioavailability- the rate at which a substance is absorbed or becomes
available at site.
2. Bioremediation Chambers - chambers at which the water treatment is done.
These are located within Estero de Balete.
3. Heavy metal - refers to any metallic chemical element that has a relatively
high density and is toxic or poisonous at low concentrations. Examples of
heavy metals include mercury (Hg), cadmium (Cd), arsenic (As), chromium
(Cr), thallium (Tl), and lead (Pb).
4. Odor - is caused by one or more volatilized chemical compounds, generally at
a very low concentration, that humans or other animals perceive by thesense
of olfaction.
5. Oxygen-Releasing Compound (ORC or biominerals) – is the medium used
in water treatment which is designed specifically to release oxygen, in a
controlled fashion, into groundwater to stimulate cost effective in situ
bioremediation of contaminants. In this study, the ORC used is a calcium-
based compound.
6. Powder Dispersion Method - is a method of water treatment wherein the
ORC are being dispersed evenly within the bioremediation chamber
7. Sediment - is naturally-occurring material that is broken down by processes
of weathering and erosion, and is subsequently transported by the action of
fluids such as wind, water, or ice, and/or by the force of gravity acting on the
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particle itself. Sediments are most often transported by water (fluvial
processes) transported by wind (Aeolian) and glaciers. Beach sands and river
to channel deposits are examples of fluvial transport and deposition, though
sediment also often settles out of slow-moving or standing water in lakes and
oceans. Deserts and loess are examples of Aeolian transport and deposition.
Glacial moraine deposits and till are ice transported sediments.
8. Tea Bag Method - is a method of water treatment wherein the ORC is placed
in tea bags. These tea bags are distributed evenly within the bioremediation
chamber. These bags are suspended and must be of about 3-4 inches above the
chamber floor. This method is done after the Powder Dispersion Method.
9. Total Kjeldahl Nitrogen content - refers to the measure of all forms of
nitrogen (organic and inorganic). Nitrogen is an essential plant element and is
often the limiting nutrient in marine waters
10. Total Organic Carbon (TOC) - is the amount of carbon bound in an organic
compound and is often used as a non-specific indicator of water quality or
cleanliness of pharmaceutical manufacturing equipment.
11. Total Phosphorus content- is a measure of both inorganic and organic forms
of phosphorus. Phosphorus can be present as dissolved or particulate matter. It
is an essential plant nutrient and is often the most limiting nutrient to plant
growth in fresh water. It is rarely found in significant concentrations in
surface waters. It is generally reported in µg/l or mg/l. The total phosphorus
concentration in most lakes not affected by anthropogenic inputs is generally
less than 0.01 mg/l (10 µg/l).
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CHAPTER 2
REVIEW OF RELATED LITERATURE AND STUDIES
2.1 Related Literature
2.1.1 Sediments
Many of the sediments in our rivers, lakes, and oceans have been
contaminated by pollutants. Many of the contaminants were released years ago
while other contaminants enter our water every day. Some contaminants flow
directly from industrial and municipal waste dischargers, while others come from
polluted runoff in urban and agricultural areas. Still other contaminants are carried
through the air, landing in lakes and streams far from the factories and other
facilities that produced them (EPA, 1996).
Sediment is any particulate matter that can be transported by fluid flow and
which eventually is deposited as a layer of solid particles on the bed or bottom of a
body of water or other liquid. Sedimentation is the deposition by settling of a
suspended material.
Sedimentation is the tendency for particles in suspension to settle out of the
fluid in which they are entrained, and come to rest against a barrier. This is due to
their motion through the fluid in response to the forces acting on them: these forces
can be due to gravity, centrifugal acceleration or electromagnetism. In geology
sedimentation is often used as the polar opposite of erosion, i.e., the terminal end
of sediment transport. In that sense it includes the termination of transport by
saltation or true bed load transport. Settling is the falling of suspended particles
through the liquid, whereas sedimentation is the termination of the settling process.
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Sediments can become contaminated in a number of ways. Urban runoff
that discharges to surface waters often contains polycyclic aromatic hydrocarbons
(PAHs), oil and grease, and heavy metals. Agricultural runoff may contain
nutrients and pesticides. Industrial spills and releases, especially those that
occurred before controls were in place, can put product into the water. Chemicals
that are denser than water, suchas polychlorinated biphenyls (PCBs) and some
pesticides like DDT, will sink to the bottom of water bodies and directly
contaminate sediments. Atmospheric deposition of substances such as mercury is
another source of sediment contamination as is the discharge of contaminated
groundwater through the sediments to the overlying surface water (USEPA 1999
and USEPA 2005).
Categories of Sediments
Sediments can be divided into three categories; framework bed load, matrix
bed load and suspended bed load.
Framework bed load creates the structure of the bed. They are large
particles that are moved only during large flow events.
The matrix bed load refers to the part of the bed material that is small
enough to be frequently entrained by low to moderate flow but is large enough to
settle out of the water column in lower velocities. They incorporate the sand and
the silt size material.
The suspended bed load is the smallest size class of the total sediments of
the fluvial system (RCA III 1995).
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Sources of Sediments and Sediment Contaminants
Aquatic sediments are principally derived from weathering processes, with
major transportation from terrestrial sources under high runoff from storms and
floods. In addition, discharges from urban, industrial and mining activities are
potential sources of particulates. Anthropogenic contaminants, including metals,
organics and nutrient elements are associated with particulate and dissolved inputs
to natural waters. It is important to distinguish between point source and diffuse
inputs. (Australian and New Zealand Guidelines for Fresh and Marine Water
Quality Volume 2, 2000)
A point source is an input that enters a body of water at a definitive
location and can usually be quantified. Factories (industrial) and municipal
wastewater outfalls are examples of point source discharges. Wastewater sources
may include domestic wastewater infiltration and inflow, and wastewater from
commercial sources such as canneries, agricultural operations, etc. Non-point or
diffuse sources, on the other hand, are discharges that cannot be identified as
coming from one definitive location or point. The discharge often enters the
waterways through overland runoff, through a large number of smaller drainage
pipes, or by precipitation travelling through the surface of the land and water.
2.1.2 Effects of Heavy Metal Contamination in Human Health and the
Environment
Contaminated sediments may be directly toxic to aquatic life or can be a
source of contaminants for bioaccumulation in the food chain. A wide range of
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physical, chemical, and biological factors have the potential to influence the
bioavailability of sediment contaminants (EPA 2004).
Sediment load values are of great ecological importance for an aquatic
system, as they influence turbidity, nutrient concentrations, the absorption of toxic
substances, and bed form characteristics.
Cadmium (Cd)
Cadmium in nature commonly occurs as a sulphide ore, usually found in
association with zinc ores such as sphalerite (CCREM 1987). Cadmium is
economically recoverable only when it occurs in association with zinc-, lead- and
copper-bearing. The principal use of cadmium is as an alloy in electroplating, in
nickel-cadmium batteries, solders, electronic equipment, photography supplies,
glass, ceramics, and plastics (CCREM 1987).
The major anthropogenic sources to the aquatic environment are through
emissions to air and water from mining and smelting and in the manufacture of the
products noted above. Additional losses occur from agricultural uses and from the
burning of fossil fuels (CCREM 1987).
In water, cadmium generally occurs in the Cd(II) form as a constituent of
inorganic (halides, sulphides, oxides) and organic compounds (CCREM 1987).
Cadmium in the water column can exist as free ions (small amount) or complexed
to various ligands such as humic acids, organic particles and various oxides.
Transport of cadmium to the sediments occurs mainly through sorption to organic
matter and subsequent settling, and through coprecipitation with iron, aluminum,
and manganese oxides. Cadmium can also be deposited in sediments through ion
exchange (mainly with calcium) on minerals. These phases account for most of the
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sediment-bound cadmium. Cadmium can also exist in sediments as free ions in the
sediment pore water, as well as bound to other sediment fractions. Sediment pore
water concentrations seem to be controlled by the solubility of iron and manganese
oxyhydroxides in the oxidized layer (particularly as these dissolve under the
advent of reducing conditions) and metal sulphides in the sulphide layer (Moore et
al 1988).
Copper (Cu)
Copper occurs naturally in rocks and minerals either as native copper, or,
more commonly, as a mineral ore. More than 160 copper containing minerals have
been described (CCREM 1987). Since copper is a common element in rock,
weathering of rock can release significant amounts to water. The uses of copper are
highly varied, but principal uses are in alloys, electroplating, electrical wiring,
paints, and pesticides. Copper in aquatic systems can exist in four oxidation states,
of which Cu (I) and Cu (ll) are the most common. Cu (I) under aerobic conditions
is readily oxidized to Cu (II). In natural waters copper undergoes complex
reactions and can be present in solution, either as cupric ions or complexed with
inorganic or organic ligands. Copper is transported to the sediments most often in
association with organic matter, and as precipitates of hydroxides, phosphates and
sulphides. Copper in sediments has a high affinity for hydrous iron and manganese
oxides, clays, carbonate materials and organic matter, though the formation of
these complexes is pH and redox dependent. Under normal pH and inorganic
carbon, most of the copper appears to be present in the form of organic complexes,
cupric carbonate complexes and coprecipitation with iron and manganese oxides
(Brook & Moore 1988; CCREM 1987).
Copper in reducing sediments is primarily in the form of sulphide
complexes, while in the oxidized zone it is mainly present as organic complexes or
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bound to hydrous iron and manganese oxides. Therefore, under anaerobic
conditions, Cu is generally immobilized in the sediments. Release of copper from
sediments can be either through ion exchange, solubilization of the matrix (e.g.
flux of Fe/Mn oxides under reducing conditions) or decomposition of the matrix
(i.e. organic matter). Since copper is an essential micronutrient, it is readily
accumulated by aquatic organisms, especially the lower animals, but no evidence
exists for bio magnification. Some evidence exists to suggest that some organisms
can limit the uptake of copper generally through increases in depuration rates
(Luoma 1983).
Lead (Pb)
Lead occurs naturally as a constituent in a variety of minerals. The single
largest use of lead is in the production of lead-acid batteries, and secondarily, in
the production of chemical compounds such as tetraethyl leads. Other uses include
ammunition manufacturer, paints, glassware, electroplating, electronic equipment,
plastics, solder, specialized containers and construction materials. Weathering of
lead minerals is the principal natural source of lead to the environment.
Anthropogenic sources include street runoff, mining and smelting operations, and
sewage treatment plants. Three oxidation states are of particular environmental
importance in aquatic systems, though of these, Pb (II) is the most stable ionic
species. Transport of lead to sediments is mainly through coprecipitation with
hydrous iron and manganese oxides, complexation with clays (which can also
contain appreciable amounts of iron and manganese hydroxides) and sorption to
organic matter. In sediments, much of the lead is found in association with the
Fe/Mn hydroxides. In oxidized sediments lead is strongly bound to the hydroxide
and organic matter fractions of the sediments. Under reducing conditions lead can
be released to the water column or can form sulphides as the Fe and Mn oxides
dissolve.
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Lead can be bioaccumulated by aquatic organisms. Organisms held at
lower pH (approx. 6.0) accumulated more lead than at higher pH presumably due
to the greater availability of divalent lead at these pH levels. Pb (n) appears to be
the most bioavailable species. In general, the organic forms (e.g. tetraethyllead)
appear to be the most bioavailable.
Mercury (Hg)
Mercury is a toxic substance which has no known function in human
biochemistry or physiology and does not occur naturally in living organisms.
Monomethylmercury is probably the most common toxic form of mercury found in
the marine environment. It has been known to travel through marine food chains
and causes damage to human consumers. All mercury that is released in the
environment will eventually end up in soils or surface waters.
2.1.3 Sediment Quality Guidelines
a. Ontario Ministry of Environment Screening Level Guidelines
The Ontario Ministry of Environment developed sediment quality
guidelines based on screening level concentrations from data for a range of local
sediments and benthic biota (ANZECC, 2000). The ministry had set three levels of
guidelines, the no-effect-level or NEL, the low-effect-level or LEL and the severe-
effect-level or SEL.
The NEL is point at which the chemicals in the sediments do not affect fish
or sediment-dwelling organisms. There is no expected effect on the water quality
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for there is no transfer of chemicals on the food chain. This level is considerably
clean. The LEL is the lowest that toxic effects become apparent and the SEL
represents concentrations that could effectively eliminate most of the benthic
organisms and pollutes the sediments. If the sediment is above SEL, testing must
be made to find out if the sediment is acutely toxic.
In line with the three levels of guidelines, the levels of contaminations for
possible metals and nutrient contents were set by Ontario Ministry of
Environment. Values are shown in Tables 2.1 and 2.2.
Table 2.1 Ontario Ministry of Screening Level Guidelines
Contaminant Lowest Effect
Level (ppm)
Severe Effect
Level (ppm)
Metals
Copper 16 110
Lead 31 250
Cadmium 0.6 10
Mercury 0.2 2
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Table 2.2 Ontario Sediment Quality Benchmarks
Nutrients Lowest Effect
Level (ppm)
Severe Effect
Level (ppm)
Total Phosphorus 600 2000
Total Kjeldahl Nitrogen 550 4800
Total Organic Carbon 1% 10%
The levels of effect are designed to help environmental managers determine:
when sediment may be considered clean;
what levels of contamination are acceptable for short periods of time while
the source of the contamination is being controlled and cleanup plans are
being developed;
what levels of contamination are considered severe enough to consider the
possibility of either removing the sediment or covering it with a layer or two
of cleaner sediment; This is called capping.
The three levels of effect are:
The No Effect Level: This is the level at which the chemicals in the
sediment do not affect fish or the sediment-dwelling organisms. At this level
no transfer of chemicals through the food chain and no effect on water
quality are expected.
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Sediment that has a No Effect Level rating is considered clean and no
management decisions are required. Furthermore, it may be placed in rivers
and lakes provided it does not physically affect the fish habitat or existing
water uses - for example a water intake pipe.
The Lowest Effect Level: This indicates a level of contamination which has
no effect on the majority of the sediment-dwelling organisms. The sediment
is clean to marginally polluted.
Dredged sediments containing concentrations of organic contaminants -
PCBs or pesticides, for example - that fall between the No Effect Level and
the Lowest Effect Level may not be disposed of in an area where the
sediment at the proposed disposal site has been rated at the No Effect Level
or better.
Contamination in sediment that exceeds the Lowest Effect Level may require
further testing and a management plan.
The Severe Effect Level: At this level, the sediment is considered heavily
polluted and likely to affect the health of sediment-dwelling organisms. If the
level of contamination exceeds the Severe Effect Level then testing is
required to determine whether or not the sediment is acutely toxic.
At the Severe Effect Level a management plan may be required. The plan
may include controlling the source of the contamination and removing the
sediment.
b. Hong Kong Sediment Quality Guideline
The Sediment Quality Guidelines of Hong Kong were primarily adopted or
modified from the United States and other temperate countries even though Hong
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Kong is located in the tropics. Hong Kong also has unique climate and hydrology
that make adopting SQGs from other countries not desirable. Unlike most tropical
countries, Hong Kong has marked seasonality with warm, wet summers and cold,
dry winters.
The Sediment Quality Guideline values were derived from an extensive
international database including effects range low (ERL), effects range median
(ERM), and the Puget Sound Estuary Program. The chemical classes currently
measured include metals, metalloids, PAHs, PCBs, and tributylin. Two SQGs were
developed for each chemical or class of chemicals. The lower chemical exceedance
level (LCEL) represents a value below which contaminants in the sediment are not
expected to have adverse biological effects, whereas the upper chemical
exceedance level (UCEL) represents a value above which toxicity is likely.
Table 2.3 Sediment quality guideline values Lower Concentration Exceedance
Level (LCEL) and Upper Concentration Exceedance Level (UCEL) of
Hong Kong
Contaminant Lower Chemical
Exceedance Level (ppm)
Upper Chemical
Exceedance Level
(ppm)
Metals
Lead 75 110
Mercury 0.5 1
Copper 65 270
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2.1.4 Bioremediation
Bioremediation can be defined as any process that uses microorganisms,
fungi, green plants or their enzymes to return the natural environment altered by
contaminants to its original condition. Aerobic Bioremediation is the practice of
adding oxygen to groundwater and/or soil to increase the number and vitality of
indigenous microorganisms performing biodegradation, calcium peroxide and
magnesium peroxide is often used as injection material.
The activity of naturally occurring microbes is stimulated by circulating
water-based solutions through contaminated soils to enhance in situ biological
degradation of organic contaminants or immobilization of inorganic contaminants.
Nutrients, oxygen, or other amendments may be used to enhance bioremediation
and contaminant desorption from subsurface materials.
Through bioremediation, soil lightly contaminated with petroleum
hydrocarbons is inoculated with a nutrient and an engineered bacterium that
combine to break down the contaminants. The bacteria access the nutrients, which
have attached to the hydrocarbons, and quickly and thoroughly degrade the
contaminants. The average time needed to reduce contaminants to acceptable
levels through bioremediation is approximately 7 to 14 days. The bioremediation
process provides substantial cost savings when compared to thermal desorption or
chemical fixation, and is typically used on soil with lower levels of contaminants.
Materials treated through bioremediation are typically beneficially re-used as fill
material.
Biological stimulants are often used to enhance the natural attenuation of
environmental contaminants. Bioremediation products are commercially used to
attenuate such contaminants as fuel hydrocarbon constituents and organic solvents
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that may be biologically transformed or immobilized under aerobic conditions. The
dissolved oxygen released from such products transforms/immobilizes the
contaminants. For this reason, a slow dissolved oxygen release is preferred to
increase contact with the contaminants dissolved in groundwater or adsorbed onto
the formation matrix. A fast release is ineffective when trying to remove the
contaminants. For example, magnesium peroxide / calcium peroxide is a potential
stimulant for contaminant attenuation. However, upon hydration these peroxides
tend to disassociate rapidly. In fact, magnesium/calcium peroxide can release their
entire dissolved oxygen load within a few weeks of hydration. For optimum use,
such stimulants must release dissolved oxygen slowly over a longer period of time,
on the order of months and not weeks. There are other compounds, such as MgO2,
CaO2, that slowly release oxygen when chemically bonded with phosphate. This
release of oxygen is a chemical process. Again, if the oxygen is released too fast,
the compound is useless as a bioremediation product. While chemically-bonded
products can solve the time-releasing problem, such compounds can be costly to
manufacture and use in large amounts. Magnesium Peroxide has the active oxygen
level as 10% commercially but Calcium Peroxide provides active oxygen level as
16%.
Bioremediation techniques have been successfully used to remediate soils,
sludge, and ground water contaminated with petroleum hydrocarbons, solvents,
pesticides, wood preservatives, and other organic chemicals.
2.1.5 Total Organic Carbon
Total organic carbon has a major influence on both the chemical and
biological process that take place in sediments. The amount of organic carbon has
a direct role in determining the redox potential in sediment, thus regulating the
behavior of other chemical species such as metals. Sources of organic carbon
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include organic matter from overland runoff and shoreline erosion (mostly
marshes), and primary productivity within the bays, all of which eventually settle
to the bay bottom and are incorporated into the sediment. Too much organic matter
can lead to the depletion of oxygen the sediment and overlying water, which can
have a deleterious effect on the benthic and fish communities. Total organic
carbon (TOC) content in sediments has been used as an indicator of pollution and
eutrophication rate (Folger 1972; EPA 2002).
2.1.6 Total Phosphorus
Phosphorus occurs naturally in rocks and other mineral deposits. During
the natural process of weathering, the rocks gradually release the phosphorus as
phosphate ions which are soluble in water and the mineralize phosphate
compounds breakdown. Phosphates are formed from this element. Phosphates
exist in three forms: orthophosphate, metaphosphate (or polyphosphate) and
organically bound phosphate each compound contains phosphorous in a different
chemical arrangement. These forms of phosphate occur in living and decaying
plant and animal remains, as free ions or weakly chemically bounded in aqueous
systems, chemically bounded to sediments and soils, or as mineralized compounds
in soil, rocks, and sediments.
Phosphorus is one of the key elements necessary for growth of plants and
animals and in lake ecosystems it tends to be the growth limiting nutrient. The
presence of phosphorus is often scarce in the well-oxygenated lake waters and
importantly, the low levels of phosphorus limit the production of freshwater
systems (Ricklefs, 1993).Unlike nitrogen, phosphate is retained in the soil by a
complex system of biological uptake, absorption, and mineralization. Phosphates
are not toxic to people or animals unless they are present in very high levels.
Digestive problems could occur from extremely high levels of phosphate. The
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soluble or bio-available phosphate is then used by plants and animals. The
phosphate becomes incorporated into the biological system but the key areas
include: ATP, DNA, and RNA; ATP, adenosine triphosphate, which is important
in the storage and use of energy and a key stage in the Kreb's Cycle. RNA and
DNA are the backbones of life on this planet, via genetics. Therefore the
availability of phosphorous is a key factor controlling photosynthesis.
Phosphate will stimulate the growth of plankton and aquatic plants which
provide food for larger organisms, including: zooplankton, fish, humans, and other
mammals. Plankton represents the base of the food chain. Initially, this increased
productivity will cause an increase in the fish population and overall biological
diversity of the system. But as the phosphate loading continues and there is a
build-up of phosphate in the lake or surface water ecosystem, the aging process of
lake or surface water ecosystem will be accelerated. The overproduction of lake or
water body can lead to an imbalance in the nutrient and material cycling process
(Ricklefs, 1993). Eutrophication (from the Greek - meaning "well nourished") is
enhanced production of primary producers resulting in reduced stability of the
ecosystem; excessive nutrient inputs, usually nitrogen and phosphate, have been
shown to be the main cause of eutrophication over the past 30 years. This aging
process can result in large fluctuations in the lake water quality and trophic status
and in some cases periodic blooms of cyanobacteria.
The non-point sources of phosphates include: natural decomposition of
rocks and minerals, stormwater runoff, agricultural runoff, erosion and
sedimentation, atmospheric deposition, and direct input by animals/wildlife;
whereas: point sources may include: wastewater treatment plants and permitted
industrial discharges. In general, the non-point source pollution typically is
significantly higher than the point sources of pollution. Therefore, the key to sound
management is to limit the input from both point and non-point sources of
phosphate.
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2.1.7 Total Kjeldahl Nitrogen
Nitrogen itself is not hazardous when present in water, and therefore does
not cause any environmental damage. In seawater nitrates, nitrites and ammonia
are dietary requirements for plankton, causing nitrogen concentrations to be lower
at the surface than in the deep. At increasing nitrogen concentrations in surface
layers, plankton production increases, leading to algal blooms. This may occur in
any type of surface water. Large amounts of nitrate may cause eutrophication,
which means an excess of nutrients resulting in oxygen deprivation and fish deaths
(see oxygen and water). Nitrogen does not limit algal growth, because phosphorus
is generally a limiting factor in water bodies. This means that phosphorus is the
determining factor of algal spreading through surface waters. Oxygen deficits in
surface water generally result in nitrate reduction to elementary nitrogen or nitrous
oxide.
Total Kjeldahl Nitrogen or TKN is the sum of organic nitrogen, ammonia
(NH3), and ammonium (NH4+) in the chemical analysis of soil, water, or
wastewater (e.g. sewage treatment plant effluent). To calculate Total Nitrogen
(TN), the concentrations of nitrate-N and nitrite-N are determined and added to
TKN.TKN is determined in the same manner as organic nitrogen, except that the
ammonia is not driven off before the digestion step.
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2.1.8 Equipment
Atomic Absorption Spectrophotometer (AAS)
Atomic Absorption Spectrophotometer is designed to determine the
presence and concentrations of metals in sediment samples. Metals include Cd, Cu,
Pb, and Hg, Cd. Typical concentrations range in the low mg/L (ppm) range. The
light of a specific wavelength is passed through the atomic vapor of an element of
interest, and measurement is made of the attenuation of the intensity of the light as
a result of absorption. Quantitative analysis by AA depends on the accurate
measurement of the intensity of the light and the assumption that the radiation
absorbed is proportional to atomic concentration. Metals will absorb ultraviolet
light in their elemental form when they are excited by heat, either by flame or
graphite furnace. Each metal has a characteristic wavelength that will be absorbed.
The AAS instrument looks for a particular metal by focusing a beam of UV light at
a specific wavelength through a flame and into a detector. The sample of interest is
aspirated into the flame. If that metal is present in the sample, it will absorb some
of the light, thus reducing its intensity. The instrument measures the change in
intensity. A computer data system converts the change in intensity into an
absorbance.
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2.2 Related Studies
Heavy Metal Contamination in Sediments
A study conducted by Sukiman B. Sarmani determines the heavy metals in
water, suspended materials and sediments from Langat River, Malaysia states the
distribution of heavy metals in the Langat River were studied for a period of six
months. Heavy metals such as arsenic, cadmium, cerium, cobalt, chromium,
cesium, lanthalium, rubidium, antimony scandium and zinc were determined in
water suspended materials and sediments samples from Langat River by neutron
activation and atomic absorption spectrometry.
A study was conducted by Ahmad et al. (2009) to determine the
concentration of selected heavy metals in Sungai Kelantan, Kelantan, Malaysia.
The river water quality was measured together with metal concentrations in
sediments in order to confirm to quality of the river. Result of water quality
analysis indicated that Sungai Kelantan is characterized by excellent water quality.
Total metal concentrations in sediment were lower as compared to the
concentration in earth crust for baseline concentration for heavy metals.
Dr. Walter Gossler and AnilaNeziri of University of Shkodra, Albania
conducted a study about the monitoring of heavy metals in water and sediment
samples from Drini River, Buna River and Lake Shkodra. From the results of
analysis of sediments from Shkodra Lake, River Drini and River Buna by using
two methods of extraction and analyzing them in ICP-MS for total concentration
of toxic metals as Copper and Cadmium, they concluded that sites in river Drini
and Buna are most contaminated from these metals which indicated in water
quality Shkodra lake and posted a risk for lake Buta. The most probable results are
geological construction from North Albania and the existing of the considerable
number of mines near Drini River.
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Nutrient Content of Sediments
Determination of total Phosphorus, total Nitrogen and Nitrogen Fractions
by Dr. Enno The task of this desk study is to give a survey over the existing
standards and the state of the art of the determination of total nitrogen (Dumas),
Kjeldahl nitrogen, the nitrogen fractions and total phosphorus. The evaluation of
the possibility of proposing draft standards for the fields of soil, sludge, bio waste
and related wastes for the respective nutrients should be the outcome. The
assessment of the existing standards shows that partly acceptable descriptions
exist. They are related to one field only e.g. soil or e.g. sludge. The different
materials require different proceedings and especially the homogeneity has to be
considered. The high demands on analytical quality and the respective validation
have to be satisfied. The result of this desk study is presented in four separate draft
standards for the determination of Kjeldahl nitrogen, total nitrogen (Dumas), the
extraction of nitrogen fractions and total phosphorus. The necessary work to
validate these standards to fulfill the high demands on analytical quality for all
applications described in the corresponding scope is pronounced.
Bioremediation
A review about Bioremediation has been argued to be one of the most cost-
effective remediation technologies available to reduce soil, sediment, or
groundwater contamination, particularly because this approach may allow for the
implementation of in-place strategies. This has been prepared by P. Adriaens, M.-
Y. Li and A. M. Michalak Recent entitled Scaling Methods of Sediment
Bioremediation Processes and Applications. Trends have advocated the application
of innovative sediment stabilization strategies through placement of (reactive)
capping material to allow long-term biodegradation of contaminants in these
complex biogeochemical environments. The potential long-term risk reduction
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associated with this approach requires a demonstration of causal relationships
between sediment or contaminant stability on the one hand, and microbial
reactivity on the other. The spatial analysis needed to fully understand and quantify
these correlations requires sensitive probabilistic techniques. This work will be
used to develop an uncertainty-based spatial decision tool for site remediation in
this watershed using various capping strategies.
A study entitled Developments in Bioremediation of Soils and Sediments
Polluted with Metals and Radionuclides by Henry H. Tabak, US EPA, ORD,
Environmental Research Center, National Risk Management Research Laboratory,
Land Remediation and Pollution Control Division, Cincinnati and Terry C. Hazen,
Lawrence Berkeley National Laboratory, Virtual Institute for Microbial Stress and
Survival, Earth Sciences Division, Ecology Dept. Berkeley. This paper will
provide a review of published research on field studies on bioremediation of metal
and radionuclide contaminated soils and sediments. The paper will (1) cite
examples of field research and cases of field in-situ bioremediation of metal and
radionuclide contaminated soils and sediments; (2) discuss the role of
phytoremediation in the treatment of metal and radionuclide contaminated soils;
and (3) provide information on the use and field-scale application of surfactants in
the treatment of metal and radionuclide pollution of soils and sediments. The
following metal-microbe interactions that impact bioremediation of metal
contamination in soils and that can be applied to field-scale biotreatment will be
discussed: Biotransformation (bioreduction and biooxidation); (2) bioaccumulation
and biosorption; (3) biodegradation of chelators; (4) biosurfactants and
biologically-assisted soil washing; (5) volatilization; and (6) biotreatment trains
and natural attenuation. The paper will also discuss research on the treatment of
metal contaminated soils, wetlands and mine areas with the use of biosolids, by
providing information on (1) in-situ soil treatments to reduce phyto- and
bioavailability of metals and (2) the use of biosolids to restore metal contaminated
mining areas impacted by metal tailings. The last 15 years have seen an increase in
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the types of contaminants to which bioremediation is being applied, including
solvents, PAHs and PCBs. Now, microbial processes are beginning to be used in
the cleanup of radioactive and metallic contaminants of soils and sediments.
Microorganisms can interact with these contaminants and transform them from one
chemical form to another by changing their oxidation state through the addition of
(reduction) or moving (oxidation) of electrons.
In some bioremediation strategies, the solubility of the transformed metal
or radionuclide increases, thus increasing the mobility of these contaminants and
allowing them to more easily be flushed out from the environment. In other
strategies, the transformed metal or radionuclide may precipitate out of the
solution, leading to immobilization. Both kinds of transformations present
opportunities for bioremediation of metals and radionuclides in the environments;
either to immobilize or to accelerate their removal. Metal contamination of soils
and sediments is especially problematic because of the strong adsorption of many
metals to their particles. Due to the difficulty of desorbing metal contaminants,
some traditional remediation methods, simply immobilize metals in contaminated
soils, by the addition of cement or chemical fixatives, by capping with asphalt, or
by in-situ vitrification. Alternatively, soils are often isolated by excavation and
confinement in hazardous waste facilities. Although rapid in effect, both of these
options are expensive and destroy soil’s future productivity. The success of soil
washing and pump-and-treat technologies to remove metals is severely limited by
the slow desorption kinetics of adsorbed metals, with the result that additional
additives (acids, chelates and reductants) are often used to promote metal transfer
to the aqueous phase. These agents improve cost effectiveness but may introduce
further harmful chemicals. A primary strategy of bioremediation is the use of
similar metal-immobilizing agents in conjunction with soil washing, with
advantage that they pose no known environmental threat themselves. Biopolymers
have been discovered that bind metals with high affinity and travel relatively
unimpeded through porous medium. Certain microorganisms transform strongly-
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adsorbing metal species into more soluble forms and plants are being recruited that
act as self-contained pump-and-treat systems. Other methods employ enzymatic
activities to transform metal species into volatile, less toxic or insoluble forms.
Techniques for soil bioremediation are usually designed to be used in-situ,
lowering costs; they avoid the use of toxic chemicals and in nearly all cases, the
soil structure and potential for productivity are preserved.
Accumulation Rate of Sediments
A study entitled Estimating accumulation rates in manila Bay, a marine
pollution hot spot in the Seas of East Asia Study by E.Z. Sombrito,A.dM,
Bulos,F.P. Siringan and E.J. Sta Maria, they identify Manila Bay as among the
marine pollution hot spots in the East Asia. Pb lead dating of its sediments can
provide a historical perspective of its pollution loading. However, the validity of
Pb dating in a complex dynamic coastal system of Manila Bay may come into
Questions. Land-based sediment input can be high and physical and biological
processes can possibly disturb the sediment layers. In this report, the Pb profiles of
sediment core from different parts of the variable across the bay. The largest
change in sedimentation rate coincided with the occurrence of a volcanic eruption
in 1991 and is shown by applying a variant of the CIC model in sedimentation rate
calculations. The data suggest that Pb dating can be very useful in estimating
relative magnitudes of sedimentation rates, even in a complex dynamic coastal
system like Manila Bay.
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CHAPTER 3
METHODOLOGY
3.1 Description of Study Area
Bioremediation chambers are located along Estero de Balete. The three
chambers are 5.7 ft high and have an area of about 222.71 ft2.
Figure 3.1a Bioremediation
Chambers
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Experimental Design
3.2 Preparation of Sampling Bed and Containers
Sampling bed are composed of frame made of a wood 1 ft. by 1 ft. dimensions
and the filter bed made of filter cloth (katsa), assembled manually. The filter beds are
weighed individually in a Top Load Balance. Containers for sediments subjected to
heavy metal analysis were cleaned by washing with distilled water.
Figure 3.1b Experimental Design for the Determination of
Accumulation Rate
CHAMBER
2
SEDIMENTS
CHAMBER
1
POINT
1 POINT
2
POINT
3
POINT
1 POINT
2
POINT
3
Figure 3.2 Sampling Bed
Wood Frame
1 ft by 1 ft
Filter
Bed
1 in
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Figure 3.3 Sampling Points for Determination of Accumulation Rate
Chamber 2
8 ft 1 in
14 ft 7 in
Chamber 1
●
●
●
8 ft 1 in
14 ft 8 in
●
●
●
3.3 Selection of Sampling Site
Sampling beds were diagonally arranged in the chamber as shown in Figure 5.
The filter beds were placed before the treatment process.
3.4 Collection of Sediment Samples
For the determination of accumulation rate of sediments, samples were taken
from each chamber every 22 days in a 2-month period, as water from each chamber is
transferred from one chamber to another every month. Filter beds were lifted up when
the water level is already about one foot above the ground of the chamber. The cloth,
which contains the sediments, was sun dried and then weighed.
Sediments, which are subjected for the analysis of heavy metal content and
nutrient content, were collected by getting samples from random sites within the
chamber. Samples, in the form of sludge, were placed in pet bottles. Overlying water
was eliminated from the pet bottle. All samples were kept at 4°C and then sent to a
DENR accredited private laboratory for analysis.
The following methods were used by the government accredited private
laboratory for the sediment analysis:
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Table 3.4 Methods Used for the Analysis of Total Phosphorus, Total Organic
Carbon, Total Nitrogen and Heavy Metals
Contaminant Method Used
Heavy Metals
Copper Flame AAS
Cadmium Flame AAS
Lead Flame AAS
Mercury Manual Cold Vapor AAS
Nutrient Content
Total Organic Carbon Ascorbic Acid Method/
Titrimetric Method
Total Phosphorus Stannous Chloride Method/
Titrimetric Method
Total Kjeldahl Nitrogen Kjeldahl Method
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CHAPTER 4
DATA PRESENTATION, ANALYSIS AND INTERPRETATION OF RESULTS
The data obtained from the experiment were presented, analyzed and
interpreted in this chapter to determine the effect of the bioremediation treatment on
the physical and chemical properties of sediments of Estero de Balete. The results of
analyses from the second run of the test were analyzed here because more considerable
change on the properties of sediments was observed than in the first run.
4.1 Physical Properties of Collected Sediments
The sediments collected from the chamber, using Powder Dispersion Method,
was observed to have light greenish gray color while the sediments from the chamber,
using Tea Bag Method, have dark greenish gray color. The light color in the Powder
Dispersion Method was mainly due to the presence of unmixed biominerals in the
collected sediments. The odor of sediments collected from the chamber both have
“fishy” odor. The odor may be attributed to the occurrence of algae buildup inside the
chamber.
Physical
Property
Powder Dispersion Method
(Chamber 1)
Tea Bag Method
(Chamber 2)
Color Light Greenish
gray
Dark greenish
gray
Odor Fishy Fishy
Table 4.1 Physical Properties of Collected Sediments
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7.7
2.4 2.5
ND 0.1 ND ND ND 0
1
2
3
4
5
6
7
8
9
Powder Dispersion Method Tea Bag Method
Co
nce
ntr
atio
n (
pp
m)
Copper Lead Cadmium Mercury
ND - Not Detected (below reporting limits)
4.2 Heavy Metal Concentrations of Collected Sediments
Heavy metals which are in high concentrations are toxic to plants and animals.
Figure 4.2 shows the heavy metal concentrations of the collected sediments after
undergoing bioremediation treatment.
The results show a decrease in the heavy metal content after the treatment.
Copper content was reduced by 70%. Cadmium and lead after Tea Bag Method were
below the reporting limits. This means that amounts of cadmium and lead are
insignificant and thus, it can be concluded that the collected sediments had negligible
amounts of the cadmium and lead after the remediation. Mercury contents were also
found to be below the reporting limits right after the first treatment. This could mean
that the sediments from the Estero de Balete hold a very small amount of mercury.
The decrease in the heavy metal content can mainly be attributed to the
reaction occurred between the biominerals and the heavy metal species in the
Figure 4.2 Graphical Representation of Heavy Metal Concentrations of
Collected Sediments
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54
37
24
2.7 1.23 0.84
0
10
20
30
40
50
60
Powder Dispersion Method Tea Bag Method
Co
nce
ntr
ati
on
(p
pm
)
Total Kjeldahl Nitrogen Total Organic Carbon Total Phosphorus
sediments. In the first treatment, the biominerals were in direct contact with the
sediments. This caused the heavy metals to precipitate and coagulate inside the
chamber. The particles that built up were then settled at the bottom. Apparently, when
the wastewater was transferred to the second chamber, lesser amount of sediments had
come with. Therefore, as expected, heavy metal analysis for the first method would be
much higher than for the second.
4.3 Nutrient Content of Collected Sediments
Nutrients in sediments such as Total Organic Carbon, Total Kjeldahl Nitrogen
and Total Phosphorus are essential in the growth of organisms. However, excess
amount of these nutrients in a waterway can lead to low levels of dissolved oxygen
and negatively alter various plant life and organisms. In this study, the nutrient
contents are tested to show the effectiveness of the ORC used in reducing excessive
amounts of nutrients in sediments.
Figure 4.3 Graphical Representation of Nutrient Concentrations of
Collected Sediments
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110
16 7.7
2.4
0
20
40
60
80
100
120
SEL LEL Powder Dispersion
Method
Tea Bag Method
Co
nce
ntr
ati
on
(p
pm
)
Copper
Figure 4.3 shows the concentrations of Total Nitrogen, Total Phosphorus, and
Total Organic Carbon concentrations after the treatment. Decrease in the nutrient
content was observed after using the two methods. Total Nitrogen and Total
Phosphorus contents were both reduced by just about 32% and the Total Organic
Carbon contents were reduced by 89%.
4.4 Assessment of Collected Sediments using Sediment Quality Guidelines
4.4.1 Ontario Ministry Sediment Quality Guideline
The purpose of the Ontario Ministry Sediment Quality Guidelines is to
protect the aquatic environment by setting safe levels for metals, nutrients
(substances which promote the growth of algae) and organic compounds. The
comparisons of the concentrations of contaminants in the sediments collected with
the Ontario Ministry Sediment Quality Guidelines are shown below.
Figure 4.4a Comparison of Copper Concentration from the
Collected Sediments with Ontario Sediment Quality Guidelines
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250
31
2.5 ND 0
50
100
150
200
250
300
SEL LEL Powder Dispersion
Method
Tea Bag Method
Co
nce
ntr
ati
on
(p
pm
)
Lead
ND - Not Detected (below reporting limits)
Figures 4.4a shows the comparison of copper concentrations from the
collected sediments with Ontario Sediment Quality Guidelines. Copper in
sediments and in water in is usually associated with tubing & plumbing which
water comes into contact with. The figure shows that the concentrations of copper
after the treatment were below the LEL value of Ontario Sediment Quality
Guidelines which means that it cause no serious effect to the environment.
Figure 4.4b describes the comparison of lead concentrations from
sediments collected with the Ontario Sediment Quality Guidelines. Lead, a metal
found in natural deposits, is commonly found on some consumer products such as
paint and children’s toys. Lead contamination may be caused by disposal of lead-
containing objects to Estero de Balete. The figure above shows that concentrations
of lead were below the LEL values of Ontario Sediment Quality Guidelines.
Hence, lead concentrations after the treatment pose no threat to the surroundings.
Figure 4.4b Comparison of Lead Concentration from the Collected
Sediments with Ontario Sediment Quality Guidelines
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10
0.6 0.1 ND
0
2
4
6
8
10
12
SEL LEL Powder Dispersion
Method
Tea Bag Method
Co
nce
ntr
ati
on
(p
pm
)
Cadmium
ND - Not Detected (below reporting limits)
Figure 4.4c represents the comparison of cadmium concentrations tested
with the LEL and SEL values of Ontario Sediment Quality Guidelines. Cadmium
is a natural, usually minor constituent of surface and groundwater. Cadmium
contamination may be caused by weathering and erosion of soils and bedrock and
improper disposal of cadmium-containing waste. Based on the figure,
concentrations of cadmium after treatment were lower than the LEL value of
Ontario Sediment Quality Guidelines. Thus, cadmium concentration can be
considered to present little or no ecological effects.
Figure 4.4c Comparison of Cadmium Concentration from the
Collected Sediments with Ontario Sediment Quality Guidelines
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2
0.2
ND ND 0
0.5
1
1.5
2
2.5
SEL LEL Powder Dispersion
Method
Tea Bag Method
Co
nce
ntr
ati
on
(p
pm
)
Mercury
ND - Not Detected (below reporting limits)
Figure 4.4d describes the comparison of mercury concentrations of the
sediments collected with Ontario Sediment Quality Guidelines. It shows that
concentrations of mercury were insignificant after treatment so, apparently,
mercury concentrations were below the LEL values and therefore, it pose no
serious threat in the surrounding.
In brief, heavy metal concentrations were below the Low and Severe Effect
Levels of Ontario Ministry Sediment Quality Guideline. This means that the
collected sediments now have a No Effect Level rating. Therefore, the sediments
are now considered clean and no management decisions are required. The OMSQ
Guideline suggests that the sediments in Estero de Balete may be placed in rivers
and lakes provided it does not physically affect the fish habitat or existing water
uses.
Figure 4.4d Comparison of Mercury Concentration from the
Collected Sediments with Ontario Sediment Quality Guidelines
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4800
550
54 37 0
1000
2000
3000
4000
5000
6000
SEL LEL Powder Dispersion
Method
Tea Bag Method
Co
nce
ntr
ati
on
(p
pm
)
Total Kjeldahl Nitrogen
2000
600
1.23 0.84 0
500
1000
1500
2000
2500
SEL LEL Powder Dispersion
Method
Tea Bag Method
Co
nce
ntr
ati
on
(p
pm
)
Total Phosphorus
Figure 4.4e Comparison of Total Kjeldahl Nitrogen Concentration
from the Collected Sediments with Ontario Sediment Quality
Guidelines
Figure 4.4f Comparison of Total Phosphorus Concentration from
the Collected Sediments with Ontario Sediment Quality Guidelines
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100000
10000
24 2.7 0
20000
40000
60000
80000
100000
120000
SEL LEL Powder Dispersion
Method
Tea Bag Method
Co
nce
ntr
ati
on
(p
pm
)
Total Organic Carbon
Figures 4.4d, 4.4e and 4.4f describe the comparison of Total Kjeldahl
Nitrogen, Total Phosphorus and Total Organic Carbon concentrations of the
sediments collected after the treatment with the Ontario Sediment Quality
Guidelines. Nutrient concentrations were below the Lowest Effect Level values of
the Ontario Sediment Quality Guideline. Therefore, the nutrient concentrations
after the treatment have no effect on water quality.
Figure 4.4g Comparison of Total Organic Carbon Concentration
from the Collected Sediments with Ontario Sediment Quality
Guidelines
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270
65
7.7 2.4 0
50
100
150
200
250
300
UCEL LCEL Powder Dispersion
Method
Tea Bag Method
Co
nce
ntr
ati
on
(p
pm
)
Copper
ND - Not Detected (Below Reporting Limits)
4.4.2 Hong Kong Sediment Quality Guideline
The sediment quality, according to its level of toxicity, is determined with
the use of the Hong Kong Sediment Quality Guideline. Analyses using this
guideline are as follows.
Copper concentrations found on the collected sediments were below the
LCEL of the Hong Kong sediment quality guideline s shown in Figure 4.4h. This
implies that copper content after treatment are not expected to have adverse
biological effects.
Figure 4.4h Comparison of Copper Concentration from the
Collected Sediments with Hong Kong Sediment Quality Guideline
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110
75
2.5 ND 0
20
40
60
80
100
120
UCEL LCEL Powder Dispersion
Method
Tea Bag Method
Co
nce
ntr
ati
on
(p
pm
)
Lead
ND - Not Detected (Below Reporting Limits)
Figure 4.4i shows the comparison of lead concentration from the sediments
collected with Hong Kong Sediment Quality Guideline. Amount of lead after the
treatment were below 75 ppm which is the LCEL value of Hong Kong Sediment
Quality Guideline. Thus, the lead concentrations are not expected to cause
unfavorable environmental effects.
Figure 4.4i Comparison of Lead Concentration from the Collected
Sediments with Hong Kong Sediment Quality Guideline
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1
0.5
ND ND 0
0.2
0.4
0.6
0.8
1
1.2
UCEL LCEL Powder Dispersion
Method
Tea Bag Method
Co
ncen
tra
tio
n (
pp
m)
Mercury
ND - Not Detected (Below Reporting Limits)
Figure 4.4i shows the comparison of lead concentration from the sediments
collected with Hong Kong Sediment Quality Guideline. Detected amounts of
mercury were too small after the treatment. Perceptibly, the concentrations of
mercury were below the LCEL value of the Hong Kong sediment quality guideline
which means that adverse biological effects are doubtful.
Figure 4.4j Comparison of Mercury Concentration from the
Collected Sediments with Hong Kong Sediment Quality Guideline
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4.5 Accumulation Rate of Sediments
Table 4.5 shows the accumulation rate of sediments in chamber 1 (Powder
Dispersion Method) and chamber 2 (Tea Bag Method). As expected, the accumulation
rate in chamber 1 is higher than chamber 2. This is evident since chamber 1 contains
more amounts of sediments. In chamber 1, sediments were mixed up with the
dispersed biominerals. Consequently, large particles were formed and settled at the
bottom. Larger particles are more likely to have faster settling rate. Given that the
biominerals used in chamber 2 were not in direct contact with the sediments, it can be
concluded that sediments in this chamber has smaller particle size. Therefore, it would
have lesser settling rate.
Method Used
1st Run
2nd
Run
Average
Powder
Method
596.05 mg/ m2 ·
hr
294.82 mg/ m2·
hr
445.4 mg/ m2·
hr
Tea Bag
Method
-
30.89 mg/ m2·
hr
30.89 mg/ m2·
hr
Table 4.4: Average weight of sediments in each filter bed
Table 4.5 Accumulation Rate of Sediments in each Filter Bed per Unit Area
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CHAPTER 5
SUMMARY OF FINDINGS, CONCLUSIONS AND RECOMMENDATIONS
5.1 Summary of Findings
The sediment samples collected were subjected to metals and nutrient
content analysis done by a government accredited laboratory. Table 5.1 shows the
summary of contaminant analyses in comparison with the two Sediment Quality
Guidelines: Ontario Sediment Quality Guidelines and Hong Kong Sediment
Quality Guideline.
*ND – Not Detected (Below Reporting Limits)
Contaminant
Method Used
Cu Pb Cd Hg TKN TP TOC
Powder Method 7.7 2.5 0.10 ND* 54 1.23 24
Tea Bag Method 2.4 ND ND ND 37 0.84 2.7
Ontario
Sediment
Quality
Guidelines
Lowest 16 31 0.6 0.2 550 600 1%
Severe 110 250 10 2 4800 2000 10%
Hong Kong
Sediment
Quality
Guideline
LCEL 65 75 - 0.5 - - -
UCEL 270 110 - 1 - - -
Table 5.1 Concentrations of Lead, Mercury, Copper, Cadmium and Nutrients from
Sediments Collected after the Bioremediation Treatment and from
Sediment Quality Guidelines (ppm)
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5.2 Conclusions
The accumulated sediments in the treatment chambers were observed to
have greenish gray color and have a fishy odor. This observation can mainly be
attributed to the algae growth as the remediation goes on.
Based on the results obtained, the mean heavy metal levels after the
remediation test provided an array of Cu>Pb>Cd>Hg. After the treatment,
significant amounts of Copper in sediments were still present while the presence of
Lead, Cadmium and Mercury was not detected. The concentrations of all the metal
contaminant are below the Lowest Effect Level values of Ontario Sediment
Quality Guidelines and Lower Concentration Exceedance Level values of Hong
Kong Sediment Quality Guideline. Therefore, these metals pose no significant
effect to the environment and adverse biological effects are very much doubtful.
Also, the nutrient concentrations of the collected sediments are found to be
of favorable amounts. After the treatment, the concentrations of Total Kjeldahl
Nitrogen, Total Phosphorus and Total Organic Carbon are below the lower
threshold limits of Ontario Sediment Quality Guidelines and Hong Kong Sediment
Quality Guideline. Thus, these nutrients pose no serious threat to the surrounding.
The average accumulation rate of the sediments in the first (Powder
Dispersion Method) and second (Tea Bag Method) chamber was found to be 445.4
mg/m2•h and 30.89 mg/m
2•h, respectively.
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5.3 Recommendations
Based on the observations, we recommend a further study on the copper
content of the sediments from estero. Even though the copper concentrations were
below the lower threshold limit of the sediment quality guidelines, a
comprehensive outline of its source must be provided. Further research on how the
copper content will completely remove from the sediments must be done.
It is recommended to identify the presence of other heavy metals such as
chromium and zinc to verify the quality of the treated sediments. Also, other
properties of the sediments such as Polychlorinated Biphenyls (PCBs) must be part
of future studies.
It is also recommended to run more trials to validate the efficiency of the
bio-remediation medium used.
Further research on other remediation techniques must be done so we can
provide evidence that Estero de Balete still holds its hope for the existence of
future biodiversity.
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APPENDICES
Appendix A: Results of Analyses
Run 1
Date of Sampling: December 17, 2010
Test Description Results Units Reporting
Limits Test Methods
Chamber 1 (Powder Dispersion Method)
Cadmium ND* mg/L 0.01 Flame AAS
Copper 9.9 mg/L 0.04 Flame AAS
Lead ND mg/L 0.07 Flame AAS
Mercury 0.03 mg/L 0.0002 Manual Cold
Vapor AAS
Total Kjeldahl
Nitrogen 36 mg/L 1.0
Titrimetry
(Kjeldahl Method)
Phosphate-P 2.0 mg/L 0.05 Stannous Chloride
Method
Total Organic Carbon 4.87 % w/w 0.10 Titrimetry
Chamber 2 (Tea Bag Method)
Cadmium ND mg/kg 0.20 Flame AAS
Copper 0.52 mg/kg 0.80 Flame AAS
Lead ND mg/kg 1.4 Flame AAS
Mercury 0.03 mg/kg 0.007 Manual Cold
Vapor AAS
Total Kjeldahl
Nitrogen 33 mg/L 1.0
Titrimetry
(Kjeldahl Method)
Phosphate-P 1.1 mg/L 0.05 Stannous Chloride
Method
Total Organic Carbon 4.47 % w/w 0.10 Titrimetry
*ND = Not Detected (Below Reporting Limits)
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Run 2
Date of Sampling: January 28, 2011
Test Description Results Units Reporting
Limits Test Methods
Chamber 1 (Powder Dispersion Method)
Cadmium 0.1 mg/L 0.01 Flame AAS
Copper 7.7 mg/L 0.04 Flame AAS
Lead 2.5 mg/L 0.07 Flame AAS
Mercury ND* mg/L 0.10 Manual Cold
Vapor AAS
Total Kjeldahl
Nitrogen 54 mg/L 1.0
Titrimetry
(Kjeldahl Method)
Phosphate-P 24 mg/L 2.0 Stannous Chloride
Method
Total Organic Carbon 1.23 % w/w 0.02 Titrimetry
Chamber 2 (Tea Bag Method)
Cadmium ND mg/kg 0.20 Flame AAS
Copper 2.4 mg/kg 0.80 Flame AAS
Lead ND mg/kg 1.4 Flame AAS
Mercury ND mg/kg 0.1 Manual Cold
Vapor AAS
Total Kjeldahl
Nitrogen 37 mg/L 1.0
Titrimetry
(Kjeldahl Method)
Phosphate-P 2.7 mg/L 2.0 Stannous Chloride
Method
Total Organic Carbon 0.84 % w/w 0.02 Titrimetry
*ND = Not Detected (Below Reporting Limits)
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Appendix B: Calculation of Accumulation Rate of Collected Sediments
Treatment Chamber Weight of Sediments (grams)
Chamber 1
(Powder Dispersion Method)
Area = 0.5056 m2
48.7 14.3 22.9
Chamber 2
(Tea Bag Method)
Area = 0.5781 m2
2.2 3.8 3.0
Treatment Chamber Weight of Sediments (grams)
Chamber 1
(Powder Dispersion Method)
Area = 0.5056 m2
88.7 61.4 9.02
Table B.2 Weight of Sediment Samples in Each Filter Bed (Second Run)
Table B.1 Weight of Sediment Samples in Each Filter Bed (First Run)
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First Run:
Chamber 1
( )
Second Run:
Chamber 1
( )
Chamber 2
( )
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Appendix C: Research Images
Treatment Chamber
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\
Collection of Filter Beds
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Sediment Sample
Sediment Sampling
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Storage of Sample
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The Researchers
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Appendix D: References
A. Books
Mudroch A, Azcue JM & Mudroch P 1997. Manual of Physico-chemical Analysis of
Aquatic Sediments. Lewis Publishers, Boca Raton, FL.
USEPA. 2005. Contaminated Sediment Remediation Guidance for Hazardous Waste
Sites, EPA-540-R-05-012. Office of Superfund Remediation and Technology
Innovation, 236 pp.
USEPA. 1999. Introduction to Contaminated Sediments. EPA 823-F-99-006, Office of
Science and Technology, 24 pp.
S.L. Simpson, 2005, Handbook for Sediment Quality Assessment.
B. Journals
García-Villalobos, Francisco Javier, Distribution of Total Organic Carbon and Total
Nitrogen in Deep-Sea Sediments from the southwestern Gulf of Mexico.
Gossler, W. And Neziri, A., Determination of heavy metals in water and sediments of
Drini River, Buna River and lake Shkodra, 2002
Johengen, T., Standard Operating Procedures for Determining Total Phosphorus,
Available Phosphorus, and Biogenic Silica Concentrations of Lake Michigan
Sediments And Sediment Trap Material
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Prudente M., Ichihashi H., and Tatsukawa Ryo., 1994. Heavy Metal Concentrations in
Sediments from Manila Bay, Philippines and Inflowing Rivers.
Riba I., DelValls T.A., Forja J.M., Go´mez-Parra, A., 2002. Influence of the
Aznalco´llar mining spill on the vertical distribution of heavy metals in
sediments from the Guadalquivir estuary (SW Spain). Mar. Pollut. Bull. 44,
39–47.
Sta. Maria E.J., Siringan F.P., BulosA.dM. And Sombrito E.Z., 2009.Estimating
sediment accumulation rates in Manila Bay, a marine pollution hot spot in the
Seas of East Asia.
Sombrito, E.Z., Siringan, F.P., and Sta.Maria,E.J., Estimating sediment accumulation
rates in Manila Bay, a marine pollution hot spot in the Seas of East Asia,
Marine Pollution Bulletin,2009
C. Electronic Sources
Brian A. Schumacher, Ph.D., Methods for the determination of Total Organic Carbon
(TOC) in soils and sediments, Retrieved September 29, 2010, from
http://www.epa.gov/esd/cmb/research/papers/bs116.pdf
Delia, C.F. et al "Nitrogen and Phosphorus Determinations in Estuarine Waters: A
Comparison of Methods Used in Chesapeake Bay Monitoring", Report
prepared for Chesapeake Bay Program Liaison Office, Region III, US EPA,
Annapolis, MD. 1987.
Exeter Analytical, Inc., Retrieved September 29, 2010, from
http://www.exeteranalytical.com/tn210.htm
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Potential Sources of Contamination. Retrieved January 29, 2011 from
http://www.njdwsc.com/prbwmp/wma3/doc/wca_report/wma3wca_3-1.pdf
USGS Bear Lake Project, 1998, Retrieved September 29, 2010, from
http://esp.cr.usgs.gov/info/lacs/lead.htm
Technical Guidance for Screening contaminated Sediments, 1999, Retrieved
September 29, 2010, from
http://www.dec.ny.gov/docs/wildlife_pdf/seddoc.pdf
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Banta, Mhadel Arguelles Address: 1627 Receiver 1st St. Phase 4, CAA Compound
Las Piñas City, Metro Manila
Mobile: +639463151634
E-Mail: [email protected]
OBJECTIVE: To offer my service and my talent to the best of my ability to a
professional organization and share my knowledge in Chemical
Engineering promoting team approach for the success of
organization.
EDUCATION:
School/Location Inclusive Date Degree
Adamson University 2006-Present BS ChE
Ermita, Manila
Rizal Technological University 2003-2004 BS ECE
Mandaluyong City
Parañaque National High School 1999-2003 Secondary
Parañaque City
Baclaran Elementary School Central 1993-1999 Elementary
Parañaque City
SPECIAL SKILLS: Computer Literate (Ms Word, Ms Excel, Auto-CAD)
Good in oral and written communication
Persuasive and hardworking
WORK EXPERIENCE: Date SERVICE CREW Nov. 2005 – April 2006
Jollibee Food Corporation
Zapote, Las Piñas City
SERVICE CREW April 2005 – Oct. 2005
Jollibee Food Corporation
Baclaran Terminal, Parañaque City
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Personal Vitae:
Sex : Female
Date of Birth : January 11, 1987
Place of Birth : Batangas
Civil Status : Single
Nationality : Filipino
Languages : Filipino & English
Affiliations:
Philippine Institute of Chemical Engineers (PIChE), Member
Adamson University Chemical Engineering Student Society
(AdUChESS), Member
Physics Society of Adamson University (PSAU), Member
CHARACTER REFERENCES:
Engr. Merlinda A. Palencia
Chairperson, Chemical Engineering Department Adamson University (632) 524-2011 loc. 410 Engr. Jerry G. Olay
Faculty Member, Chemical Engineering Department Adamson University (632) 524-2011 loc. 410
I hereby certify that the information above is true and correct to the best interest of my
knowledge.
ARGUELLES BANTA
Applicant
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Camille G. Candelaria 8 Doña Juana Subd. 3 Santolan Pasig city 1610 (+63)927-300-8208 [email protected]
Objective
To seek a challenging and rewarding opportunity where I can fully utilize my skills and experiences gained from my education and seminars
Education
Tertiary Adamson University
2006 - present
900 San Marcelino St., Ermita Manila B.S., Chemical Engineering
University Of Nueva Caceres June 2004-March 2006 Jaime Hernandez Avenue Naga City B.S., Electrical Engineering
Secondary
University of Nueva Caceres 2000 - 2004 Jaime Hernandez Avenue Naga City Graduation date: March 2004
Primary
University of Nueva Caceres 1994 - 2000
Jaime Hernandez Avenue Naga City Graduation date: March 2000
Personal Information
Birthday: April 16, 1987 Status: Single Citizenship Filipino Religion: Catholic Skills: Good communication Skills Computer litera
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I hereby swear that the above information is true.
Candelaria, Camille G. Applicant
Affiliates
Secretary, Womens Club (UNC Chapter) Secretary, LigangNagkakaisang Mag-aaral Para saAktibongPamunuan (LINGAP Member, Philippine Institute of Chemical Engineers (PIChE)
Member, Adamson University Chemical Engineering Student Society (AdUChESS)
Member, Physics Society of Adamson University (PSAU)
References
Engr. Merlinda Palencia
Chairperson, chemical Engineering Department Adamson University
Engr. Jerry Olay
Professor Adamson University
Melinda Candelaria Production Supervisor Ashford Pharmaceutical Laboratory Inc.
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Pagasartonga, Mon Eric P. #18 Gerodias St., San Vicente, San Pedro, Laguna 0927-6962880 [email protected] Objective: To have the opportunity to have hands-on experience on the theoretical concepts that I have learned, familiarizing me with the various industrial operations and unit process Personal Vitae
Age: 21
Sex: Male
Date of Birth: March 30, 1990
Place of Birth: San Pedro, Laguna
Nationality: Filipino
Civil Status: Single
Height: 5’5”
Weight: 117 lbs
Educational Background
School Year Graduated
B.S. Chemical
Engineering
Adamson University
900 San Marcelino St., Ermita, Manila
Secondary San Francisco de Sales School
101 National Highway, San Pedro,
Laguna
2006
Primary San Pedro Central School
San Pedro, Laguna
2002
Affiliations
Philippine Institute of Chemical Engineers (PIChE), Member
Adamson University Chemical Engineering Student Society (AdUChESS),
Member
Physics Society of Adamson University (PSAU), Member
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Skills
Computer Literate (knowledgeable in Microsoft Office Applications)
Willing to learn
Character References April M. Patricio, R.Ph.
Pharmacist Generika Drugstore, Montillano, Alabang 0916-3244678
Engr. Merlinda A. Palencia
Chairperson, Chemical Engineering Department Adamson University (632) 524-2011 loc. 410
Engr. Jerry G. Olay
Faculty Member, Chemical Engineering Department Adamson University (632) 524-2011 loc. 410
I hereby certify that the information above is true and correct to the best interest of my knowledge.
MON ERIC PAGASARTONGA
CHEMICAL ENGINEERING
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Ricarte, Shienah Coronado Blk.4 Lot 19 Palmera Springs 3-B, Camarin, Caloocan City
Email: [email protected] Mobile No.: 0935-9849828
Objective:
To have a challenging position in chemical engineering where I could apply all major principles and my specialized interested areas of application namely thermodynamics, fluid dynamics by which I can apply my wide knowledge and professional expertise in the field of chemical engineering.
Educational Attainment:
Adamson University
Ermita, Manila Bachelor of Science in Chemical Engineering 2004-present
St.Clare College of Caloocan
Zabarte rd.,Camarin Caloocan City
High School Graduate (3rd honour) 2001-2004
Bagong Silang Elementary
Elementary Graduate 1995-2000
Work Experience:
Grand Asia Food Corporation (Jollibee-Zabarte)
588 Camarin corner Zabarte Road (North), Caloocan City Administrative Crew July-December 2006
LOJ Food Corporation (Jollibee-Nova Quirino)
938 Quirino Highway, Novaliches, QC Service Crew December-May 2007
Achievements and Skills:
Adamson University Chemical Engineering Students Society (AdUChESS),
Member
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Liga ng Nagkakaisang Mag-aaral tungo sa aktibong Pamunuan
(LINGAP),Secretary
Physics Society of Adamson University (PSAU), Member
10th Outstanding Student for the School Year 2007-2008
(Chemical engineering Department)
Adamson University Academic Scholar Grantee (2nd sem,2007-2008)
Good computer skills (MS Office Applications and the Internet)
Outgoing, Persistent and Articulate
Willing to learn
Eager to contribute and be motivated to succeed
Personal Data: Age : 23 years old Gender: Female Citizenship : Filipino Civil Status: Single Birth date : January 23, 1987 Birth Place: Manila Height : 5’1 Weight: 90 lbs. Language : English, Tagalog Father’s name : Leonardo U. Ricarte Occupation: OFW Mother’s name: Ma.Rowena C. Ricarte Occupation: Teacher & Real State Dealer Sibling’s name: Ma. Sheila C. Ricarte Sarah Hazel C. Ricarte
Ma.Sheilinah C. Ricarte John Gerald C. Ricarte
Reference:
Engr.Jerry G. Olay
Professor, Chemical Engineering Department Adamson University
Beverly C. Samia
Bureau of Internal Revenue
Engr.Rommel Galvan
Professor, Chemical Engineering Department Adamson University I hereby swear that the above information is true.
Shienah Ricarte