Wetland construction seminar REPORT

Wetland construction

1. INTRODUCTION

1.1 GENERAL

Globally, most of the developing countries are geographically located in those parts of

the world that are or will face water shortages in the near future. Moreover, the existing water

sources are contaminated because untreated sewage and industrial wastewater is discharged into

surface waters resulting in impairment of water quality. The treatment of wastewater using

Constructed Wetland (CW) is one of the suitable treatment systems, used in many parts of the

world. Wetlands are defined as land where the water surface is near the ground surface long

enough each year to maintain saturated soil conditions, along with the related vegetation.

Marshes, bogs, and swamps are all examples of naturally occurring wetlands.

A “constructed wetland” is defined as a wetland specifically constructed for the purpose

of pollution control and waste management, at a location other than existing natural wetlands .

Wetlands can be used for primary, secondary, and tertiary treatments of domestic wastewater,

storm wastewater, combined sewer overflows (CSF), overland runoff, and industrial wastewater

such as landfill leachate and petrochemical industries wastewater. The most common systems are

designed with horizontal subsurface flow (HF CWs) but vertical flow (VF CWs) systems are

getting more popular at present. The most commonly used species are robust species of emergent

plants, such as the common reed, cattail and bulrush.

In this seminar paper the inlet and outlet wastewater physico-chemical parameters were

analysed during the retention period. The parameters studied were pH, BOD, COD, DO, Total

Suspended Solids, Total Dissolved Solids, Nitrogen and Phosphorus. The percentage removal of

the parameters were analysed and studied until the percent removal rate gets stabilized.

1.2 ADVANTAGES OF CONSTRUCTED WETLANDS

Wetlands can be less expensive to build than other treatment options

Utilization of natural processes,

Simple construction (can be constructed with local materials),

Simple operation and maintenance,

cost effectiveness (low construction and operation costs),

Dept. of Civil Engineering, M.E.S College of Engineering, Kuttippuram


Process stability.

Low energy demand.

Low environmental impact

1.3 LIMITATIONS OF CONSTRUCTED WETLANDS

large area requirement

wetland treatment may be economical relative to other options only where land is

available and affordable.

Design criteria have yet to be developed for different types of wastewater and climates.

1.4 NATURAL WETLANDS VS. CONSTRUCTED WETLANDS

A natural wetland is an area of ground that is saturated with water, at least periodically.

Plants that grow in wetlands, which are often called wetland plants or saprophyte, have to be

capable of adapting to the growth in saturated soil.

Constructed wetlands, in contrast to natural wetlands, are man-made systems or

engineered wetlands that are designed, built and operated to emulate functions of natural

wetlands for human desires and needs. Engineered to control substrate, vegetation, hydrology

and configuration. It is created from a non-wetland ecosystem or a former terrestrial

environment, mainly for the purpose of contaminant or pollutant removal from wastewater

(Hammer).These constructed wastewater treatments may include swamps and marshes. Most of

the constructed wetland systems are marshes. Marshes are shallow water regions dominated by

emergent herbaceous vegetation including cattails, bulrushes, and reeds.

Fig 1.1 A natural wetland: Tasek Bera, a freshwater swamp Fig 1.2 A constructed wetland:

Putrajaya system Wetlands



2. LITERATURE REVIEW

ATIF MUSTAFA(2013) conducted treatment performance of a pilot-scale constructed

wetland (CW) commissioned in in Karachi, NED University of Engineering & Technology, was

evaluated for removal efficiency of biochemical oxygen demand (BOD), chemical oxygen

demand (COD), total suspended solids (TSS), ammonia-nitrogen (NH4-N), ortho-phosphate

(PO4-P), total coliforms (TC) and faecal coliforms (FC) from pretreated domestic wastewater.

Monitoring of wetland influent and effluent was carried out for a period of 8 months. NED

wastewater treatment plant (WWTP) treats wastewater from campus and staff colony. The

wastewater contains domestic sewage and low flows from laboratories of various university

departments. The constructed wetland is planted with common wetland plant (Phragmites

karka). The key features of this CW are horizontal surface flow. Treatment effectiveness was

evaluated which indicated good mean removal efficiencies; BOD (50%), COD (44%), TSS

(78%), NH4-N (49%), PO4-P (52%), TC (93%) and FC (98%).

YADAV and JADHAV (2011) construct wetland unit combined with surface flow and

planted with Eichhornia crassipes was built near Technology Department, Shivaji University,

Kolhapur ( Latitude 160 40’ N, Longitude 740 15’ S). Maharashtra situated in Western part of

India. The campus wastewater was let into the constructed wetland intermittently over 30

days.The study was performed in two sets A and B which were run in the months of December

and January respectively. The parameters analysed for the study were pH, Dissolved Oxygen,

Biochemical Oxygen Demand, Chemical Oxygen Demand, Total Suspended Solids, Total

Dissolved Solids, Nitrogen and Phosphorus. Only quality of wastewater was analysed during the

study period of 2 months i.e. December and January. The sampling took place daily at both inlet

and outlet of constructed wetland system. Treatment effectiveness was evaluated which indicated

good mean removal efficiencies; BOD (95%), COD (97%), TSS (82%), NH4-N (43%), PO4-P

(49%).



3. WETLAND CONSTRUCTION

Wetlands, either constructed or natural, offer a cheaper and low-cost alternative

technology for wastewater treatment. A constructed wetland system that is specifically

engineered for water quality improvement as a primary purpose is termed as a ‘Constructed

Wetland Treatment System’ (CWTS). In the past, many such systems were constructed to treat

low volumes of wastewater loaded with easily degradable organic matter for isolated populations

in urban areas. However, widespread demand for improved receiving water quality, and water

reclamation and reuse is currently the driving force for the implementation of CWTS all over the

world. The ability of wetlands to transform and store organic matter and nutrients has resulted in

a widespread use of wetland for wastewater treatment worldwide.

Recent concerns over wetland losses have generated a need for the creation of wetlands,

which are intended to emulate the functions and values of natural wetlands that have been

destroyed. Natural characteristics are applied to CWTS with emergent macrophyte stands that

duplicate the physical, chemical and biological processes of natural wetland systems. The

number of CWTS in use has very much increased in the past few years. The use of constructed

wetlands in the United States, New Zealand and Australia is gaining rapid interest. Most of these

systems cater for tertiary treatment from towns and cities. They are larger in size, usually using

surface-flow system to remove low concentration of nutrient (N and P) and suspended solids.

However, in European countries, these constructed wetland treatment systems are usually used to

provide secondary treatment of domestic sewage for village populations. These constructed

wetland systems have been seen as an economically attractive, energy-efficient way of providing

high standards of wastewater treatment.

Typically, wetlands are constructed for one or more of four primary purposes: creation of

habitat to compensate for natural wetlands converted for agriculture and urban development,

water quality improvement, flood control, and production of food and fiber (constructed

aquaculture wetlands).

Constructed wetlands are based upon the symbiotic relationship between the micro

organisms and pollutants in the wastewater. These systems have potential to treat variety of

wastewater by removing organics, suspended solids, pathogens, nutrients and heavy Metals.



A constructed wetland is a shallow basin filled with some sort of filter material (substrate),

usually sand or gravel, and planted with vegetation tolerant of saturated conditions. Wastewater

is introduced into the basin and flows over the surface or through the substrate, and is discharged

out of the basin through a structure which controls the depth of the wastewater in the wetland. A

constructed wetland comprises of the following five major components:

• Basin

• Substrate

• Vegetation

• Liner

• Inlet/Outlet arrangement system

Fig 3.1 Components of constructed wetland(UN-HABITAT, 2008.)

Basin

Systems have been designed with bed slopes of as much 8 percent to achieve the

hydraulic gradient. Newer systems have used a flat bottom or slight slope and have employed an

adjustable outlet to achieve the hydraulic gradient.

Subsrate

Many different media sizes have been tried for the bed, but gravel less than 4 cm

diameter seems to work best. Larger diameters increase the flow rate, but result in turbulent flow.

Smaller media gives a reduced hydraulic conductivity, but has the advantage of more surface



area for microbial activity and adsorption. Soil is sometimes used to remove certain materials

due to the ability of reactive clays to adsorb heavy metals, phosphates, etc..

Vegetation

Three types of plants are normally used

Cattails, which are a favorite food of muskrats and nutria.

Bulrush is also high on the mammals food list, but they should not be attracted to the

wetland if the water surface is kept below the media.

Reeds are used most often in Europe because they are not a food source for animals.

However, they are not allowed in some areas due to their tendency to spread and push out

native vegetation.

The type used will also depend on the local climate and the substances to be removed. In some

instances decorative plants are used, but results show them to be less effective and require more

maintenance. Control of the water level can be used to increase root penetration and control

weeds.

Liner

The liner goes under the entire system and can be a manufactured liner or clay. This

prevents the wastewater from infiltrating into the ground before it is treated. A berm around the

system prevents runoff from entering the system.

Inlet

The inlet can be a manifold pipe arrangement, an open trench perpendicular to the flow,

or weir box. The manifold arrangement can be a pipe with several valve outlets or a simple

perforated pipe. Coarse gravel allows rapid infiltration of the water. The inlet purpose is to

spread the wastewater evenly across the treatment bed for effective treatment

Outlet

The outlet structures used are similar to the inlet structures. One preferred addition is making

the outlet adjustable to allow the control of water level. The level could be lowered when a large

amount of rainfall is expected or raised for maximum cross-sectional use of the media.



3.1 TYPES OF CONSTRUCTED WETLAND

CW could be classified according to the various parameters but the two most important

criteria are water flow regime (surface and sub-surface) and the type of macrophytic growth.

Different types of constructed wetlands may be combined with each other (so called hybrid or

combined systems) in order to exploit the specific advantages of the different systems. The

quality of the final effluent from the systems improves with the complexity of the facility.

Emergent macrophytes based systems can be constructed with surface flow, subsurface

horizontal flow and vertical flow (fig 3.2 )

Fig 3.2 Classification of constructed wetlands for wastewater treatment ( Vymazal and

Kropfelova, 2008)

3.1.1 SURFACE FLOW SYSTEMS

A typical surface flow (SF) or free water surface constructed wetland (FWS CW) with

emergent macrophytes (usually covering more than 50 percent), is a shallow sealed basin or

sequence of basins, containing 20-30 cm of rooting soil, with a water depth of 20-40 cm. As the

name suggests, the waste water flows above the ground exposed to the atmosphere. Inflow water



containing particulate and dissolved pollutants slows and spreads through a large area of shallow

water and emergent vegetation. FWS CW typically have aerated zones, especially near the water

surface because of atmospheric diffusion, and anoxic and anaerobic zones in and near the

sediments. In heavily loaded FWS wetlands, the anoxic zone can move quite close to the water

surface.

Long retention times and an extensive surface area in contact with the flowing water

provide for effective removal of particulate and organic matter. The sediment, plant biomass and

plant litter surfaces are also where most of the microbial activity affecting water quality occurs,

including oxidation of organic matter and transformation of nutrients. Biomass decay provides a

carbon source for denitrification, but the same decay competes with nitrification for oxygen

supply. Low winter temperatures enhance oxygen solubility in water, but slow microbial activity.

Fig 3.3 Typical configuration of a surface flow wetland system (Kadlec and Knight,1996)

3.1.2 SUB-SURFACE SYSTEMS

These systems have the water level designed to remain below the top of the substrate.

They have the added component of emergent plants with extensive root systems within the

media.

CW with sub-surface flow may be classified according to the direction of flow;

horizontal and vertical (Fig.3.2) on one hand, and into soil, sand and gravel based wetlands on

the other hand. The substratum provides the support and attachment surface for microorganisms



able to anaerobically (and/or anoxically if nitrate is present) reduce the organic pollutants into

CO2, CH3, H2S etc. The substratum also acts as a simple filter for the retention of influent

suspended solids and generated microbial solids, which are then themselves degraded and

stabilized over an extended period within the bed, such that outflow suspended solids levels are

generally limited. The provision of a suitably permeable substrate in relation to the hydraulic

loading to obviate surface ponding tends to be the most expensive component of the subsurface

flow systems, and catered for. Sub-surface systems are also referred to as planted filters, reed

beds, root zone method, gravel bed hydroponics filters, vegetated submerged beds or artificial

wetlands.

Fig 3.4 Typical configuration of a sub-surface flow system(Kadlec and Knight,1996)

3.1.2.1 HORIZONTAL FLOW SYSTEMS (HFS)

It is called horizontal flow because the wastewater is fed in at the inlet and flows slowly

through the porous medium under the surface of the bed in a more or less horizontal path until it

reaches the outlet zone where it is collected before leaving via level control arrangement at the

outlet (fig 3.6). During this passage the wastewater will come into contact with a network of

aerobic, anoxic and anaerobic zones. The aerobic zones occur around roots and rhizomes that

leak oxygen into the substrate. CW with horizontal subsurface flow requires much larger

vegetated bed area in order to effectively eliminate phosphorous and nitrogen.



HFS are very efficient in removing organic matter and suspended solids. BOD removal

rates range between 65 percent and 90 percent, with average BOD effluent concentrations below

30-70 mg/l. Typical effluent TSS levels are below 10–40 mg/l and correspond to 70–95percent

removal rates. Pathogen removal amounting to 99 percent or more (2–3 log) total coliforms has

been reported by Crites and Tchobanoglous . Tropical and subtropical climates hold the greatest

potential for the use of HFS. Cold climates tend to show problems with both icing and thawing.

Water stress of plants in a HFS is an important issue to be considered especially in households

systems during periods without inflow (e.g. during holidays).

Fig 3.5 Horizontal flow constructed wetland

Fig3.6 Schematic cross-section of horizontal flow constructed wetland (Morel and

Diener ;2006)



3.1.2.2 VERTICAL FLOW SYSTEMS (VFS)

VFS are shallow excavations or above-ground constructions with an impermeable liner,

either synthetic or clay. They are characterized by intermittent (discontinuous) loading and

resting periods where the waste water percolates vertically through the substrate. Intermittent and

batch loading enhances oxygen transfer and thus nitrification. The main purpose of plant

presence in VFS is to help maintain the hydraulic conductivity of the bed. VFS have a typical

depth of 0.8–1.2m. For small systems (i.e. single households) receiving septic tank effluents,

Cooper (1999) proposes the use of two vertical –flow beds in series.

Removal efficiencies in terms of BOD, COD, ammonia-N and pathogens of VFS are

generally higher than comparable HFS. However removal of suspended solids is somewhat

lower than in HFS. Average removal efficiencies are typically within a range of 75-95percent

and 65-85 percent in terms of BOD and TSS respectively. Pathogen removal in terms of total

coliforms are typically within a range of 2-3 log and can be as high as 5 log as seen in Nepal.

This could be resolved by recycling of the effluent into the pretreatment unit, e.g. septic or

Imhoff tank (Arias and Brix, 2006).

One of the major threats of good performance of VFS is clogging of the filtration

substrate. Therefore, it is important to properly select the filtration material, hydraulic loading

rate and distribute the water evenly across the bed surface in order to avoid overloading of

certain parts of the surface. Given their reliance on a well functioning pressure distribution, they

are more adapted to locations where natural gradients can be used, thus enabling the filter by

gravity. Since flat areas require the use of pumps, they are thus dependent on a reliable power

supply and frequent maintenance.

VFS could be further categorized into down-flow and up-flow depending on whether the

wastewater is fed onto the surface or to the bottom of the wetland. VFS are primarily used to

treat domestic or municipal sewage. The system has also been successfully applied to municipal,

industrial. (Explosives, food processing, airport de-icing water, acid mine drainage) as well as

agricultural (aquaculture, swine feedlot) wastewaters (Behrends et al,1996)



Fig 3.7 Schematic cross-section of vertical flow constructed wetland( Morel and

Diener,2006)

Fig 3.8 Vertical flow constructed wetland

3.1.2.2.1 Downflow

Vertical flow constructed wetlands (VF CW) comprise a flat bed of graded gravel topped

with sand planted with macrophytes. The size fraction of gravel is larger in the bottom layer (e.g.

30-60 mm) and smaller in the top layer (e.g., 6 mm). VFCW are fed intermittently with a large

batch thus flooding the surface. Wastewater then gradually percolates down through the bed and

is collected by a drainage network at the base. The bed drains completely free and it allows air to

refill the bed. This kind of dosing leads to good oxygen transfer and hence the ability to nitrify.



Fig 3.9 Typical arrangement of a downflow vertical-flow constructed wetland ( Cooper et

al.,1999)

3.1.2.2.2 Upflow

In vertical-up flow CW the wastewater is fed on the bottom of the filter bed. The water

percolates upward and then it is collected either near the surface or on the surface of the wetland

bed.

These systems have commonly been used in Brazil. The beds are filled with crushed rock

on the bottom, the next layer is coarse gravel and the top layer is soil planted with Rice (Oryza

sativa). This treatment system is called in Brazil ―filtering soil‖ (Fig 3.10). However, outside

Brazil, the layer of soil is usually not used and beds are filled with gravel and usually planted

with common species such as Phragmites australis.



Fig 3.10 Schematic representation of a constructed wetland with vertical up-flow

( Vymazal.2001)

3.1.2.2.3 Tidal flow

Tidal flow systems are a new form of. Tidal flow systems were developed to try to

overcome some of the problems that were seen in the early forms of VFS related to clogging of

the surface. Upflow systems have been used for about 20 years but they suffer from the problem

that distribution is below the surface and hence hidden from the observers.

In tidal flow systems at the start of the treatment cycle the wastewater is fed to the

bottom of the bed into the aeration pipes. It then percolates upwards until the surface is flooded.

When the surface is completely flooded the pump is then shut off, the wastewater is then held in

the bed in contact with the micro-organisms growing on the media. A set time later the

wastewater is drained downwards and after the water has drained from the bed the treatment

cycle is complete and air diffuses into the voids in the bed.

3.1.2.3 HYBRID SYSTEMS

Various types of CW may be combined in order to achieve higher treatment effect,

especially for nitrogen. In these systems, the advantages of the HSF and VF systems can be

combined to complement each other. Therefore, there has been a growing interest in hybrid

systems (also sometimes called combined systems). Hybrid systems used to comprise most

frequently VFS and HFS arranged in a staged manner (fig 3.11); however, all types of CW could

be combined. In hybrid systems, the advantages of various systems can be combined to



complement each other. It is possible to produce an effluent low in BOD, which is fully-nitrified

and partly denitrified and hence has much lower total-N concentrations.

The design consists of two stages of several parallel VF beds (―filtration beds‖)

followed by 2 or 3 HF beds (―elimination beds‖) in series. The results indicate very good

removal for organics (BOD5 and COD) and TSS while removal of nitrogen is enhanced with no

nitrate increase at the outflow.

Fig 3.11 Schematic arrangement of the HF-VF hybrid system according to Brix and

Johansen. (Vymazal.2001)

3.2 WETLAND PLANTS

The role of wetland vegetation as an essential component of CW is well established.

Emergent plants contribute both directly and indirectly to the treatment processes. In spite of the

fact that the most important removal processes in CW are based on microbial processes, the

macrophytes posses several functions in relation to the water treatment. They influence

treatment process in CW by their physical presence and metabolism. In general, the most

significant functions of wetland plants (emergents) in relation to water purification are the

physical effects brought by the presence of the plants. The plants provide a huge surface area for

attachment and growth of microbes. The physical components of the plants stabilise the surface

of the beds, slow down the water flow thus assist in sediment. Plants also provide

microorganisms with a source of Carbon.



However, not all wetland species are suitable for wastewater treatment since plants for

CW must be able to tolerate a combination of continuous flooding and exposure to wastewater or

storm water containing relatively high amounts of pollutants. A portion of the nutrients is

retained in the undecomposed fraction of the plant litter and accumulates in the soils. Plants

oxygenate the root zone by release of oxygen from their roots, and provide aerobic

microorganisms a habitat within the reduced soil. Plants have additional site-specific values by

providing habitat for wildlife and making wastewater treatment systems aesthetically pleasing.

Wetland species of all growth forms have been used in treatment wetlands. However, the most

commonly used species are robust species of emergent plants, such as the common reed, cattail

and bulrush. The larger aquatic plants growing in wetlands are usually called macrophytes. Three

most important criteria form the basis for the plant choice:

Availability in climate zone

Pollutant removal capacity (treatment efficiency) and tolerance ranges

Plant productivity and biomass utilization options

3.2.1 PLANTS IN WETLANDS

The larger aquatic plants growing in wetlands are usually called macrophytes. The term

includes aquatic vascular plants (angiosperms and ferns), aquatic mosses, and some larger algae

that have tissues that are easily visible. Although ferns like Salvinia and Azolla and large algae

like Cladophora are widespread in wetlands, it is usually the flowering plants (i.e. angiosperms)

that dominate. Macrophytes, like all other photoautotrophic organisms, use the solar energy to

assimilate inorganic carbon from the atmosphere to produce organic matter, which subsequently

provides the energy source for heterotrophs (animals, bacteria and fungi). As a result of the

ample light, water and nutrient supply in wetlands, the primary productivity of ecosystems

dominated by wetland plants are among the highest recorded in the world. Associated with this

high productivity is usually a high heterotrophic activity, i.e. a high capacity to decompose and

transform organic matters and other substances.



The presence or absence of aquatic macrophytes is one of the characteristics used to

define wetlands, and as such macrophytes are an indispensable component of these ecosystems.

In spite of the fact that the most important removal processes in constructed treatment wetlands

are based on physical and microbial processes, the macrophytes possess several functions in

relation to the water treatment.

Vegetation and its litter are necessary for successful performance of constructed wetlands

and contribute aesthetically to the appearance. The vegetation to be planted in constructed

wetlands should fulfill the following criteria:

• Application of locally dominating macrophyte species;

• Deep root penetration, strong rhizomes and massive fibrous root;

• Considerable biomass or stem densities to achieve maximum translocation of water and

assimilation of nutrients;

• Maximum surface area for microbial populations;

• Efficient oxygen transport into root zone to facilitate oxidation of reduced toxic

metals and support a large rhizosphere.

Two species, Phragmites sp. and Typha sp., widely used vegetation in constructed wetlands.

Phragmites karka and P. australis (Common Reed) is one of the most productive, wide spread

and variable wetland species in the world.

Due to its climatic tolerance and rapid growth,

it is the predominant species used in construc-

ted wetland.



Fig 3.12 Phragmites kark (common reed)

fig 3.13 Cattail-typha angustifolia

3.2.2 SELECTION OF WETLAND PLANTS

Floating and submerged plants are used in an aquatic plant treatment system. A range of

aquatic plants have shown their ability to assist in the breakdown of wastewater. The Water

Hyacinth (Eichhornia crassipes), and Duckweed (Lemna) are common floating aquatic plants

which have shown their ability to reduce concentrations of BOD, TSS and Total Phosphorus and

Total Nitrogen. However prolonged presence of Eichhornia crassipes and Lemna can lead to

deterioration of the water quality unless these plants are manually removed on a regular basis.

These floating plants will produce a massive mat that will obstruct light penetration to the lower

layer of the water column that will affect the survival of living water organisms. This system is

colonised rapidly with one or only a few initial individuals. The system needs to be closely

monitored to prevent attack from these nuisance species. Loss of plant cover will impair the

treatment effectiveness. Maintenance cost of a floating plant system is high. Plant biomass

should be regularly harvested to ensure significant nutrient removal. Plant growth also needs to

be maintained at an optimum rate to maintain treatment efficiency.



Fig 3.14 The Water Hyacinth Eichhornia crassipes

The Common Reed (Phragmites spp.) and Cattail (Typha spp.) are good examples of

emergent species used in constructed wetland treatment systems. Plant selection is quite similar

for SF and SSF constructed wetlands. Emergent wetland plants grow best in both systems. These

emergent plants play a vital role in the removal and retention of nutrients in a constructed

wetland. Although emergent macrophytes are less efficient at lowering Nitrogen and Phosphorus

contents by direct uptake due to their lower growth rates

(compared to floating and submerged plants), their

ability to uptake Nitrogen and Phosphorus from sediment

sources through rhizomes is higher than from the water.

Fig 3.15 The Common Reed Phragmites karka

3.2.3 EXAMPLES OF WETLAND PLANTS

There is a variety of marsh vegetation that is suitable for planting in a CWTS (see Table

3.1 ). These marsh species could be divided into deep and shallow marshes.



Table 3.1: List of emergent wetland plants used in constructed wetland treatment systems

(Lim et al.1998)

Planting zones Common name Scientific name

Marsh and deep marsh (0.3-1.0m) Common Reed Phragmites karka

Spike rush Eleocharis dulcis

Greater Club Rush Scirpus grossus

Bog Bulrush Scirpus mucronatus

Tube Sedge Lepironia articulate

Fan Grass Phylidrium lanuginosum

Cattail Typha angustifolia

Shallow marsh(0-0.3m) Golden Beak Sedge Rhynchospora corbosa

Spike rush Eleocharis variegta

Sumatran Scieria Scieria Sumatran

Globular Fimbristylis Fimbristylis globulsa

Knot Grass Polygonum barbatum

Asiatic Pipewort Erioucauio longifolium

3.2.4 ROLE OF PLANTS

The main role of the aquatic plants (please be sure to select only aquatic plants because of

the always water saturated environment that is a fundamental aspect in constructed wetlands) is

to act as catalyzers in the purification process. This process, as seen before, is a combination of

microbiological, chemical and physical processes. The plants haven’t a significant action as

direct removal (for some substances, like N and P or organic matter, we can talk of a

contribution in the order of 10-20% during the vegetative season); they offer instead a very

efficient support for the growth of aerobic bacteria colonies on their rhizomes. Air is pumped

towards the root zone by several mechanisms, like convection. Another important plant’s

function is the maintenance and continuous re-establishment of the hydraulic conductivity inside

the beds. Amongst all macrophytes, Phragmites australis or communis is the most used



worldwide for its optimal performances, for its ability in developing deep roots (0.5-0.7 m), for

its resistance to aggressive wastewaters and to diseases.

Table 3.2 Role of plants (Brix, 1997)Macrophyte property Role in treatment process

Aerial plant tissue Light attenuation – reduced growth of phytoplankton

Reduced wind velocity – reduced risk resuspension

Aesthetic pleasing appearance of system

Storage of nutrients

Plant tissue in water Filtering effect-filter out large debris

Reduced current velocity –Increase rate of sedimentation, reduced

risk of suspension

Provide surface area for attached biofilms

Excretion of photosynthetic oxygen –Increases aerobic degradation

Uptake of nutrients

Roots and rhizomes in

the sediment

Stabilizing the sediment surface-less erosion

Prevents the medium from clogging in VFS

Release of oxygen increase degradation(nitrification)

Uptake of nutrients



4. REMOVAL MECHANISMS

A constructed wetland is a complex assemblage of wastewater, substrate, vegetation and an

array of microorganisms (most importantly bacteria). Vegetation plays a vital role in the

wetlands as they provide surfaces and a suitable environment for microbial growth and fi

ltration. Pollutants are removed within the wetlands by several complex

physical(sedimentation,filtration,adsorption and volatisation) chemical(precipitation, adsorption

hydrolysis, oxidation/reduction) and biological (bacterial metabolism,plant metabolism, plant

absorption,natural die-off processes as depicted in Fig 4.1

Fig 4.1 The pollutant removal mechanisms in constructed wetland (modified from

Wetlands International, 2003)

Settleable and suspended solids that are not removed in the primary treatment are eff

ectively removed in the wetland by filtration and sedimentation. Particles settle into stagnant

micro pockets or are strained by flow constrictions. Attached and suspended microbial growth is

responsible for the removal of soluble organic compounds, which are degraded biologically both

aerobically (in presence of dissolved oxygen) as well as anaerobically (in absence of dissolved

oxygen). The oxygen required for aerobic degradation is supplied directly from the atmosphere



by diffusion or oxygen leakage from the vegetation roots into the rhizosphere, however, the

oxygen transfer from the roots is negligible (Figure 4.1).

Table 4.1 the pollutant removal mechanism in constructed wetland

Waste water constituents Removal mechanism

Suspended solids Sedimentation

filtration

Soluble organics Aerobic microbial degradation

Anaerobic microbial degradation

Phosphorus Matrix sorption

Plant uptake

Nitrogen Ammonification followed by microbial

nitrification

Denitrification

Plant uptake

Matrix adsorption

Ammonia volatilazation( mostly in SF system)

Metals Adsorption and cation exchange

Complexation

Precipitation

Plant uptake

Microbial oxidation/ reduction

Pathogens Sedimentation

Filtration

Natural die-off

Predation



Fig 4.2 Oxygen transfer from roots(modified from Wetlands International, 2003)

4.1 NITROGEN REMOVAL MECHANISMS

There are sufficient studies to indicate some roles being played by wetland plants in

Nitrogen removal but the significance of plant uptake vis-à-vis nitrification/denitrification is still

being questioned. Nitrogen (N) can exist in various forms, namely Ammoniacal Nitrogen (NH3

and NH4+), organic Nitrogen and oxidised Nitrogen (NO2- and NO3-). The removal of Nitrogen

is achieved through nitrification/denitrification, volatilisation of Ammonia (NH3) storage in

detritus and sediment, and uptake by wetland plants and storage in plant biomass (Brix, 1993). A

majority of Nitrogen removal occurs through either plant uptake or denitrification. Nitrogen

uptake is significant if plants are harvested and biomass is removed from the system.

At the root-soil interface, atmospheric oxygen diffuses into the rhizosphere through the

leaves, stems, rhizomes and roots of the wetland plants thus creating an aerobic layer similar to

those that exists in the media-water or media-air interface. Nitrogen transformation takes place in

the oxidised and reduced layers of media, the root-media interface and the below ground portion

of the emergent plants. Ammonification takes place where Organic N is mineralised to NH4+-N

in both oxidised and reduced layers. The oxidised layer and the submerged portions of plants are

important sites for nitrification in which Ammoniacal Nitrogen (AN) is converted to nitrite N

(NO2-N) by the Nitrosomonas bacteria and eventually to nitrate N (NO3-N) by the Nitrobacter



bacteria which is either taken up by the plants or diffuses into the reduced zone where it is

converted to N2 and N2O by the denitrification process.

Denitrification is the permanent removal of Nitrogen from the system; however the

process is limited by a number of factors, such as temperature, pH, redox potential, carbon

availability and nitrate availability. The annual denitrification rate of a surface-flow wetland

could be determined using a Nitrogen mass-balance approach, accounting for measured influx

and efflux of Nitrogen, measured uptake of Nitrogen by plants, and sediment, and estimated NH3

volatilisation.

The extent of Nitrogen removal depends on the design of the system and the form and

amount of Nitrogen present in the wastewater. If influent Nitrogen content is low, wetland

plants will compete directly with nitrifying and denitrifying bacteria for NH4+ and NO3-, while in

high Nitrogen content, particularly Ammonia, this will stimulate nitrifying and denitrifying

activity.

Figure 4.3: Nitrogen transformations in a constructed wetland treatment system (Cooper et

al.1996)



4.2 PHOSPHORUS REMOVAL MECHANISMS

Phosphorus is present in wastewaters as Orthophosphate, Dehydrated Orthophosphate

(Polyphosphate) and Organic Phosphorus. The conversion of most Phosphorus to the

Orthophosphate forms (H2PO4-, Po42-, PO43-) is caused by biological oxidation. Most of the

Phosphorus component may fix within the soil media. Phosphate removal is achieved by

physical-chemical processes, by adsorption, complexation and precipitation reactions involving

Calcium (Ca), Iron (Fe) and Aluminium (Al). The capacity of wetland systems to absorb

Phosphorus is positively correlated with the sediment concentration of extractable Amorphous

Aluminum and Iron (Fe). Although plant uptake may be substantial, the sorption of Phosphorus

(Orthophosphate P) by anaerobic reducing sediments appears to be the most important process.

The removal of Phosphorus is more dependent on biomass uptake in constructed wetland

systems with subsequent harvesting.

4.3 BOD5 REMOVAL

The physical removal of BOD5 is believed to occur rapidly through settling and

entrapment of particulate matter in the void spaces in the gravel or rock media. Soluble BOD 5 is

removed by the microbial growth on the media surfaces and attached to the plant roots and

rhizomes penetrating the bed. Some oxygen is believed to be available at microsites on the

surfaces of the plant roots, but the remainder of the bed can be expected to be anaerobic.

4.4 PLANT UPTAKE

Nitrogen will be taken up by macrophytes in a mineralised state and incorporated it into

plant biomass. Accumulated Nitrogen is released into the system during a die-back period. Plant

uptake is not a measure of net removal. This is because dead plant biomass will decompose to

detritus and litter in the life cycle, and some of this Nitrogen will leach and be released into the

sediment. Johnston (1991) shows only 26-55% of annual N and P uptake is retained in above-

ground tissue, the balance is lost to leaching and litter fall.

4.5 METALS

Metals such as Zinc and Copper occur in soluble or particulate associated forms and the

distribution in these forms are determined by physico-chemical processes such as adsorption,

precipitation, complexation, sedimentation, erosion and diffusion. Metals accumulate in a bed



matrix through adsorption and complexation with organic material. Metals are also reduced

through direct uptake by wetland plants. However over-accumulation may kill the plants.

4.6 PATHOGENS

Pathogens are removed mainly by sedimentation, filtration and absorption by biomass

and by natural die-off and predation.

6.7 OTHER POLLUTANT REMOVAL MECHANISMS

Evapotranspiration is one of the mechanisms for pollutant removal. Atmospheric water

losses from a wetland that occurs from the water and soil is termed as evaporation and from

emergent portions of plants is termed as transpiration. The combination of both processes is

termed as evapotranspiration. Daily transpiration is positively related to mineral adsorption and

daily transpiration could be used as an index of the water purification capability of plants.

Precipitation and evapotranspiration influence the water flow through a wetland system.

Evapotranspiration slows water flow and increases contact times, whereas rainfall, which has the

opposite effect, will cause dilution and increased flow.

Precipitation and evaporation are likely to have minimal effects on constructed wetlands

in most areas. If the wetland type is primarily shallow open water, precipitation/evaporation

ratios fairly approximate water balances. However, in large, dense stands of tall plants,

transpiration losses from photosynthetically active plants become significant.

Fig 4.4 Experimental studies continue to be carried

out in Florida and many other parts of the country as well as overseas to evaluate the

performance of a variety of constructed wetlands systems.( United States EPA(2003)



5. CASE STUDY’S

5.1 CASE STUDY 1

5.1.1 EXPERIMENTAL SET UP

The constructed wetland (CW) treatment system is situated in Karachi, NED University

of Engineering & Technology, at a longitude 25° 56‘8” N and latitude 67° 06’ 44” E. The

maximum and minimum temperatures during the study period were 36° C and 20° C,

respectively. NED wastewater treatment plant (WWTP) treats wastewater from campus and staff

colony. The wastewater contains domestic sewage and low flows from laboratories of various

university departments. The primary treatment consist of a settling tank, after that the wastewater

is transferred to an aeration tank and then to a secondary settling tank. The main objective to

construct the wetland at the WWTP site is to evaluate the performance of simple and low-cost

wastewater treatment technology.

The effluent entering the CW system (cell) comes from a WWTP which treats domestic

and institutional wastewater. The key features of this CW are horizontal surface flow (HSF). The

HSF CW was selected as this kind of system does not have the clogging problem. The

constructed wetland is designed as a plug flow reactor and length to width ratio (L: W) is 4:1.

The cell design consists of a rectangular bed, bordered with masonry work of 0.25 m wall and

concrete based floor to protect seepage of wastewater. The cell is 0.30 m above and 0.30 m

below the ground, so no external water enters into the cell from the natural ground surface. The

system is designed for a flow of 1 m3/d.

The design of this pilot-scale constructed wetland consists of a bed that is rectangular in

shape and is planted with common wetland plant (Phragmites karka). Pre-treated wastewater is

fed in the storage tank placed at the influent end of the wetland; the influent entering the CW is

controlled manually by adjusting the valve attached to the inlet pipe. The flow between inlet and

outlet is by gravity. PVC pipes at the inlet and outlet zone are slotted to distribute and collect the

wastewater. This slotting method reduces short circuiting in the cell and the whole bed is utilized

to treat the wastewater. The treated wastewater from the outlet zone is collected is a small ditch

walled with masonry bricks. The inlet pipe has a diameter of 5 cm while outlet pipe diameter is



10 cm (Fig.5.1). The soil used for wetland bed was first checked that no roots of any other plants

are present. Then the cell was half filled with the soil in such a way that wastewater will flow

towards the effluent end by making inclination of 5 degrees. The bed was filled with water to

settle the soil and facilitate the growth of macrophytes. The main features of the constructed

wetland at NED University are presented in Table 5.1 while Fig. 5.1 shows the layout of CW

added to the treatment train.

Fig 5.1 Pilot scale constructed wetland layout: (1) secondary wastewater effluent from

wastewater treatment plant to storage tank, (2) control valve, (3) inlet pipe, (4) constructed

wetland (5) outlet pipe, (6) water level control box.

Table 5.1: Main features of the constructed wetland

Parameter Unit Value

Length Metre 6

Width Metre 1.5

Height Metre 0.6

Surface area Metre 9

Hydraulic retention time Days 4

Flow Cubic metre per day 1

vegetation Metre 4 plants



5.1.2 OPERATIONS

Young plants of Phragmites karka were collected from the campus surroundings in late

May, 2010. The plants were transplanted the same day in the bed at a density of four plants per

square meter. The cell was filled with fresh water so that the macrophytes adapt to the new

environment. Later on, the cell of CW was loaded with settled domestic wastewater from the

campus and staff colony. Sampling scheme was initiated after an acclimatisation period of 6

weeks.

For wastewater analysis, grab samples were collected in plastic bottles previously washed

and rinsed with distilled water. Samples were collected after every two weeks from the inlet and

outlet of the CW. Liquid samples were tested for pH, total dissolved solids (TDS), total

suspended solids (TSS), 5 days biochemical oxygen demand (BOD5) at 20°C, chemical oxygen

demand (COD), ammonia nitrogen (NH4-N) ortho-phosphate (PO4-P), temperature, dissolved

oxygen (DO), faecal coliforms (FC), total coliforms (TC) using American Public Health

Association standards methods . All samples were analysed in the laboratory of environmental

engineering department.

5.1.3 RESULT

During the eight months monitoring period which started in the month of September,

2010 and continued till late April 2011, samples were collected from the CW system and

analysed for each of the various physical, chemical and microbiological parameters. Table

presents the average inlet and outlet concentrations of each monitored parameter.



Table 5.2 : water quality variables mean ± (standard deviation) for the constructed wetland

S. No Variables Unit n Inlet Outlet Reduction(%)

1 BOD mg/L 16 68.6±23.6 34.0±15.5 50

2 COD mg/L 16 122.9±50.7 68.3±20.7 44

3 TSS mg/L 16 201.4±93.2 45±26.3 78

4 Ammonia-

nitrogen

mg/L 16 19.2±4.8 9.7±4.6 49

5 Ortho-phosphate mg/L 16 7.6±1.9 3.7±2.3 52

6 Total coliforms Counts/100mL 12 2.1x106 8x103 93

7 Faecal coliforms Counts/100mL 12 1.1x106 3x103 98

8 ph _ 16 7.8±0.7 7.9±0.4 _

9 Dissolved

oxygen

mg/L 16 1.7±0.6 4.5±1.2 _

5.2 CASE STUDY 2

5.2.1 EXPERIMENTAL SET UP

Yadav S. B., Jadhav A. S(2011) construct wetland as combined with surface flow and

planted with Eichhornia crassipes was built near Technology Department, Shivaji University,

Kolhapur. ( Latitude 160 40’ N, Longitude 740 15’ S). Maharashtra situated in western part of

India. The climate of this region is tropical with an average annual rainfall of 1025 mm. The

mean minimum and maximum temperatures during the study period were 15° C and 34°C

respectively.

The integrated subsurface flow artificial wetland constructed with brickwork of size 3 m

× 1.25m having a depth of 0.6 m. The tank is plastered in cement mortar on both sides. The

bottom of the tank is made up of 1:4:8 concrete portions to make it watertight. The necessary

slope is provided at the bottom of the tank for sludge removal. The constructed wetland cell is of

3.06 sq m area and length to width ratio 2.45:1.25. The depth of the bed is 0.6 m. The bed has

regular rectangular shape and a necessary slope is provided at the bottom of the tank for sludge

removal. The inlet and outlet chambers are made up of PVC pipe of 12.5 m in diameter with a



control valve. At the base of the wetland unit two pipes of 10 cm diameter having inward holes

at every 0.9 m distance run parallel in longitudinal direction from inlet chamber to outlet

chamber to facilitate the drainage.

OPERATIONS

The campus wastewater was let into the constructed wetland intermittently over 30 days.

The plants were monitored for general appearance, growth and health. The length of the plant

was found to be similar to that of wetland plants in natural wetlands. Any invasive plants like

ordinary grass were uprooted and removed immediately. The plant density spread vigorously

within 2 months.

RESULTS

The overall system treatment performance was high and stable during the observation period

Table 5.3: Physico-chemical parameters and percent removal at inlet and outlet of Set A.

Sl.No Parameter Inlet Outlet Average %

removalRange Average Range Averag

e

1 pH 7.1-7.4 6.3 7-7.3 7.2 -

2 DO 0 0 3.4-7.1 5.56 -

3 BOD 122-1 163.2 14-21 21.9 86.19%

4 COD 169.2-176.40 171.9 18-25 23.10 87.35%

5 TSS 135-142 167.1 20-59 41 76%

6 TDS 465-505 537 99-120 199.1 69.95%

7 TN 13.8-14.95 17.3 6.95-7.98 9.08 43.33%

8 Total

phosphorus

3.14-3.9 4.4 1.6-2.01 1.99 45%



Table 5.4: Physico-chemical parameters and percent removal at inlet and outlet of Set

Sl.No Parameter Inlet Outlet Average %

removalRange Average Range Average

1 pH 7.2-7.8 7.6 7.1-7.6 7.3 -

2 DO 0-0.1 0 4.9-6.2 7.1 -

3 BOD 132.4-141.8 136.9 9-24 22.6 95.8%

4 COD 167.4-178.8 173.45 10-28 24.9 97%

5 TSS 136.80-139.6 138.54 14-55 32.45 82%

6 TDS 467.4-486 433 90-110 109.81 71%

7 TN 14.01-14.42 14.20 7.12-7.82 6.79 43.07%

8 Total phosphorus 3.45-3.66 3.25 1.42-1.92 1.5 49.03%

Fig.2: Water Weed: Eichhornia crassipes; Fig.3: Filling the C.W. by sewage;

Fig.4: Placing the Eichhornia crssipes in the C.W.; Fig.5: Growth of Eichhornia crssipes



6. CONCLUSION

It is noted that CWs are now being increasingly used for environmental pollution control.

Recent inventories have indicated that there are more than 7000 CWs in Europe and North

America with the number increasing in Central and South America, Australia and New Zealand

as well as Asia and Africa. Most of them are local soil/gravel based systems with either

horizontal or vertical flow planted mostly with common reeds (phragmites australis).

Constructed wetlands were implemented in a wide range of applications, such as water quality

improvement of polluted surface water bodies, wastewater on-site treatment and reuse in rural

areas, campuses, recreational areas and green architectures, management of aquaculture water

and wastewater, tertiary treatment, and miscellaneous applications.

Water monitoring results obtained from several demonstrations show that CWs could

achieve acceptable wastewater treatment performances in removing major pollutants, including

suspended solids, organic matters, nutrients, and indicating microorganisms, from wastewater

influent. The results indicate that if constructed wetlands are appropriately designed and

operated, they could be used for secondary and tertiary wastewater treatment under local

conditions, successfully. Hence constructed wetlands can be used in the treatment train to

upgrade the existing malfunctioning wastewater treatment plants, especially in developing

countries. During hydraulic retention study, it was found that the BOD, COD was best removed

in planted wetland than unplanted wetland. It is because of the oxygen diffusion from roots of

the plants and the nutrient uptake and insulation of the bed surface. It is also found that the

increases in the detention period of the wastewater the removal rate also increases.



7. REFERENCE

1. Borkar.R.P , Mahatme.P.S(2011),” Wastewater Treatment with Vertical Flow Constructed

Wetland” , International journal of environmental sciences Vol 2(2), pp 590 -603

2. Asghar Ebrahimi, Ensiyeh Taheri(2013)” Efficiency of Constructed Wetland Vegetated

with Cyperus alternifolius Applied for Municipal Wastewater Treatment “, Hindawi

Publishing Corporation Journal of Environmental and Public Health, Vol. 2013,pp 1-5

3. Hafeznezami1; Jin-Lee Kim(2012)” Evaluating Removal Efficiency of Heavy Metalsh in

Constructed Wetlands”,journal of environmental engineering © asce / april 2012 ,pp 475-

482.

4. Atif Mustafa( 2013),” Constructed Wetland for Wastewater Treatment and Reuse:A Case

Study of Developing Country”, International Journal of Environmental Science an

Development, Vol. 4(1),pp 20-24

5. Yadav S. B., Jadhav A. S(2011),” Evaluation of Surface Flow Constructed Wetland System

by Using Eichhornia crassipes for Wastewater Treatment in an Institutional Complex”,

universal Journal of Environmental Research and Technology All Rights Reserved Euresian

publications ,Vol.1,pp 435-441

6 Chavan B.L, and Dhulap V.P.(2013),” Developing a Pilot Scale Angular Horizontal

Subsurface

Flow Constructed Wetland for Treatment of Sewage through Phytoremediation with

Colocasia esculenta”, International Research Journal of Environment Sciences Vol. 2(2), pp

6-14

7. Dr. joachim schrautzer, Ralph otterpohl(2009),” constructed wetlands: potential for their

use in treatment of grey water in kenya’’, environmental management management

natürlicher resourcen,pp 1-77

8. “The use of constructed wetlands for wastewater treatment”, Wetlands International - Malaysia-Office(2003)

9. “ Constructed wetland manual”, United Nations Human Settlements Programme (UN-

HABITAT),( 2008)


Wetland construction seminar REPORT

Education

Transcript of Wetland construction seminar REPORT