ArticlePDF Available

Abstract and Figures

In order to develop sustainable wastewater treatment it is needed to view the wastewater treatment systems in a broad sense. In addition to cost and treatment performance energy aspects, recycling and social issues are important when evaluating sustainability of a wastewater treatment system and selecting an appropriate system for a given condition. This requires a multidisciplinary approach where engineers cooperate with social scientists, economists, biologists, health officials and the public. Wastewater contains organic matter and the three main nutrients for plant production: nitrogen, phosphorus and potassium. Theoretically speaking, the nutrients in domestic wastewater and organic household waste are nearly sufficient to produce enough food for the world population. Nitrogen fertilizer is energy consuming to produce and phosphorus is a limited mineral resource. Recycling and energy aspects are thus important factors of sustainable system design. Scandinavia is pioneering sustainable solutions to wastewater treatment. Energy efficient moving bed reactors are developed for tertiary treatment in traditional "end of pipe" wastewater collection and treatment systems. A variety of watersaving and urine diverting toilets can nearly halve water consumption. Toilet waste (blackwater) or urin can be collected separately. Cotreatment of blackwater and organic household waste yield both energy and hygienic fertilizer and handles all organic waste from the household in one waste stream. Water from showers, sinks and kitchen (greywater) can be treated in a variety of systems. Treated greywater is suitable for irrigation, groundwater recharge or as a source of potable water production. Utilizing the latter more than 90% water saving is possible. Source separation (blackwater/greywater) systems produce near zero emissions and open up for exiting urban applications.
Content may be subject to copyright.
In: L. Seng (ed.) Proc. International conference on natural resources and environmental management
and environmetal safety and health. Kuching, Malaysia. November 27-29, 2007.
1
SUSTAINABLE WASTEWATER TREATMENT
By Petter D. Jenssen*, Lasse Vråle** and Oddvar Lindholm**
* Department of Plant and Environmental Sciences
**Department of Mathematical Sciences and Technology
Norwegian University of Life Sciences
1432 Aas, Norway
petter.jenssen@umb.no
www.ecosan.no
ABSTRACT
In order to develop sustainable wastewater treatment it is needed to view the
wastewater treatment systems in a broad sense. In addition to cost and treatment
performance energy aspects, recycling and social issues are important when
evaluating sustainability of a wastewater treatment system and selecting an
appropriate system for a given condition. This requires a multidisciplinary approach
where engineers cooperate with social scientists, economists, biologists, health
officials and the public.
Wastewater contains organic matter and the three main nutrients for plant production:
nitrogen, phosphorus and potassium. Theoretically speaking, the nutrients in domestic
wastewater and organic household waste are nearly sufficient to produce enough food
for the world population. Nitrogen fertilizer is energy consuming to produce and
phosphorus is a limited mineral resource. Recycling and energy aspects are thus
important factors of sustainable system design.
Scandinavia is pioneering sustainable solutions to wastewater treatment. Energy
efficient moving bed reactors are developed for tertiary treatment in traditional “end
of pipe” wastewater collection and treatment systems. A variety of watersaving and
urine diverting toilets can nearly halve water consumption. Toilet waste (blackwater)
or urin can be collected separately. Cotreatment of blackwater and organic household
waste yield both energy and hygienic fertilizer and handles all organic waste from the
household in one waste stream. Water from showers, sinks and kitchen (greywater)
can be treated in a variety of systems. Treated greywater is suitable for irrigation,
groundwater recharge or as a source of potable water production. Utilizing the latter
more than 90% water saving is possible. Source separation (blackwater/greywater)
systems produce near zero emissions and open up for exiting urban applications.
INTRODUCTION
In order to develop sustainable wastewater treatment it is needed to view the
wastewater treatment systems using a holistic approach. A holistic approach implies
considering the primary and secondary environmental effects and costs that the
systems produce. Examples are the pollution produced at the power plant (generating
electricity for wastewater treatment) and the energy cost of producing treatment
chemicals. Designing or selecting a treatment system based on sustainability criteria
In: L. Seng (ed.) Proc. International conference on natural resources and environmental management
and environmetal safety and health. Kuching, Malaysia. November 27-29, 2007.
2
involves a multidisciplinary approach where engineers cooperate with social scientists,
economists, biologists, health officials and the public.
Over the last decade sustainable wastewater treatment has been an issue at several
conferences (Ødegaard 1991, Henze et al. 1997, Graf 1999). The first international
conferences of “Ecological engineering for wastewater treatment”, was held in
Sweden in 1991 (Etnier and Guterstam 1991), addressing sustainable wastewater
treatment systems. The focus was on natural or ecologically engineered systems, that
optimize resource gains and minimized resource use, hence, recycling and energy
aspects, were in focus. Later several conferences have been held regarding ecological
sanitation (Staudenmann et al. 1996, Kløve et al. 1999, Jana et al. 2000, Werner et al.
2004). The year 2008 which had been declared the “Year of Sanitation” by the
United Nations to bring more focus to sanitation because the Millenium goals for
sanitation is far behind schedule to fulfill the goals. To promote sustainable sanitation
systems toward 2008 a Sustainable Sanitation Alliance (SSA 2007) was formed. The
SSA unites forces of universities working with sustainable sanitation with major
world organizations as UNDP and the world bank national donor organizations and
NGOs.
One of the first attempts to look at energy aspects of wastewater treatment was
Antonucci and Schaumburg (1975). They documented the energy and chemical use at
South Lake Tahoe tertiary treatment plant and concluded that it was impossible to say
whether the plant was an environmental benefit or liability.
The European union (EU) has launched a 5-year project COST C8 "Best Practise for
Sustainable Infrastructure" and is developing a handbook for assessing the degree of
sustainability for infrastructure of water supply and sewerage systems. In this project
15 countries are co-operating to make a push for more sustainable infrastructure.
In Norway the national research program ”Natural systems for wastewater treatment
93-98” (Jenssen 1995) had a main focus on development of sustainable systems for
rural areas. Simple wetland systems that meet tertiary standards and decentralized
systems with near complete recycling of nutrients, possibilities for large water savings
and energy production were developed (Jenssen and Etnier 1997, Mæhlum 1998, Zhu
1998, Jenssen 1999, Jenssen and Krogstad 2002, Jenssen et al. 2005). Some of these
systems are also suited in urban areas.
In Sweden a large national research program (Urban water 2001) involving all major
Swedish universities was launched at the turn of the Millenium. This 6-year project,
finances 15 doctoral candidates working only within sustainable wasterwater systems.
It is expected that this program will bring Sweden in the forefront in the world
concerning the design, analysis and operation of sustainable wastewater alternatives.
This paper briefly mentions sustainability analysis of wastewater treatment systems.
The main focus is on sustainable technologies for wastewater treatment developed in
Norway. This includes optimization of conventional technologies for nitrogen
removal based on moving bed and fixed film reactors and ammonia stripping. In
addition recycling systems based on separate treatment of the blackwater (toilet
In: L. Seng (ed.) Proc. International conference on natural resources and environmental management
and environmetal safety and health. Kuching, Malaysia. November 27-29, 2007.
3
waste) and greywater (all except toilet waste, shower, kitchen and washing) is
described (Jenssen et al. 2003). Such systems can be utilized both in rural and urban
settings.
SUSTAINABILITY ANALYSIS OF WASTEWATER TREATMENT
SYSTEMS
In earlier times and even to day, engineers and politicians nearly always use a simple
cost/benefit analysis when choosing a wastewater system. This means that, for
instance, only the discharge of organic matter (BOD) or phosphorus and the cost is
looked upon. However, the quest for sustainability is necessary because we see many
problems are coming like global warming, acidification, diminishing ozone layer,
micro-organic pollutants and other toxic chemical matters, eutrophication,
diminishing important resources like phosphorus, potassium and oil and other threats
to mankind, flora and fauna. This shows that many indicators must be used when
deciding what type of wastewater systems we should implement. And we should
choose the wastewater system that contributes most to an overall sustainable future.
The notion sustainability should include ecology, economy and sociological aspects
and the sustainability must also perform on three different stages:
1. Local, where hygienic and health aspects are of concern in time scales of hours or
days.
2. Regional, where classic environmental problems operate in time scales of months
or years.
3. Global, where sustainability matters in a time scale of decades or centuries.
To compare two wastewater alternatives the following indicators may be considered
as relevant for a sustainability analysis (Lindholm and Nordeide 2000):
Discharge of pollution to local recipients and major recipients. For instance:
phosphorus, nitrogen and organic matter (BOD).
The amount of micro-organic pollutants and heavy metals in the sludge going to
agriculture.
Amount of phosphorus, potassium and nitrogen recirculated for plant production.
Discharge of climate gases like methane and CO2.
Use of electric energy and fossil energy.
Use of products with hazardous components.
Use of finite or critical resources.
Costs as present value of investments, operation and maintenance.
The use of area, influence on the landscape, aesthetic- and recreational values.
The service levels like clogging of sewers and flooding of basements.
Noise, smell, insects and other disturbances in the operation and construction
period.
Safety for children.
Indicators that are approximately the same for both alternatives may be eliminated.
The system borders for the analysis of the sustainability of a wastewater system are
very important for the assessment. A wider or narrower definition of the system
In: L. Seng (ed.) Proc. International conference on natural resources and environmental management
and environmetal safety and health. Kuching, Malaysia. November 27-29, 2007.
4
studied may alter the result of the assessment completely. The assessment may be
studied on a global scale, on a regional/city scale or on a block/neighbourhood scale.
The two last ones are appropriate for studies of infrastructure systems, even if the
global context should be considered at all times. The system borders should be large
enough to include not only the infrastructure itself (the hardware of the system), but
also the city area it serves and the productive land and waters that enable the cycles of
nutrients to be closed (the extended system).
However, up to now we have realised that the municipalities nearly always choose the
well known, and cheapest alternative that complies with the minimum regulations and
absolute demands from the authorities. We must hope that in the future this will
change. The municipalities should achieve a minimum acceptable level of
sustainability for their wastewater systems.
RESOURCES IN DOMESTIC WASTEWATER AND ORGANIC
HOUSEHOLD WASTE
Substantial amounts of plant nutrients and organic matter are present in household
waste and waste from food processing industries (Jenssen and Skjelhaugen 1994).
Theoretically speaking, the nutrients in domestic wastewater and organic waste are
nearly sufficient to fertilize crops to feed the world population (Wolgast 1992). This,
however, requires that people turn to a vegetarian diet. It also requires that
appropriate technologies are available for safe recycling of the wastewater resources.
Practically speaking 20-40 % of the water consumption in sewered cities is used to
flush toilets (Gardner 1997). In order to evolve towards a sustainable society we need
to recycle nutrients, reduce the water consumption, and minimize the energy needed
to operate waste treatment processes.
Figures for the amount of mineral fertilizer that can be substituted for organic
fertilizer sources vary and depend on several factors, one being whether a country has
a net import or export of food. In countries belonging to the Organisation for
Economic Cooperation and Development (OECD) the nutrients in wastewater average
8 % of the applied mineral fertilizer and the nutrients in household and yard waste
constitute another 7 % (Gardner 1997). If all the nitrogen and phosphorous in
Norwegian wastewater was reclaimed and recycled into agriculture, application of
mineral fertilizer could be reduced 15-20 % (Jenssen and Vatn 1991). The
corresponding figures for Sweden are 16-17 % (Guterstam 1991). In most developing
countries these levels are higher (Gardner 1997), and according to Etnier and Jenssen
(1997) more than 40 % of the nutrients present in chemical fertilizers could,
theoretically, be substituted with nutrients from wastewater. Organic matter accounts
for one third of the input to landfills in industrialized countries and as much as two
thirds, in developing countries (Gardner 1997).
While recycling domestic organic waste can not replace mineral fertilizer entirely, it
can reduce pollution from domestic waste, reduce excessive fertilizer use and develop
healthier soils.
Tertiary treatment facilities can be designed to remove both nitrogen and phosphorous,
but recycling of the nitrogen is difficult unless nitrogen is precipitated as struvite or
In: L. Seng (ed.) Proc. International conference on natural resources and environmental management
and environmetal safety and health. Kuching, Malaysia. November 27-29, 2007.
5
removed using ammonia stripping with adsorption. The most common method of
nitrogen removal in conventional treatment plants today are biological processes.
However, with these methods most of the removed nitrogen is discharged to
atmosphere. Phosphorus is most commonly removed by chemical precipitation using
either Fe- or Al-salts as precipitating agents. However, the plant availability of
phosphorus precipitated as Fe- or Al-phosphates can be very limited due to very low
solubility under normal soil conditions whereas with lime precipitation the phosphates
are easier dissolved and available to the plants (Krogstad et al. 2005). Since
industries, households, and street runoff discharge to the same sewer system, there is a
risk of heavy metals and other contaminants. In Scandinavia, this threat has reduced
the farmer«s motivation to recycle sewage sludge.
LARGE CONVENTIONAL TREATMENT SYSTEMS
Sustainability aspects of nutrient removal (tertiary treatment)
The Norwegian Institute for Water Research (NIVA), showed in the 60`s and the 70`s,
that it was important to remove phosphorus from wastewater in Norway, because
phosphorus is the main limiting factor for algal blooms in rivers, lakes and narrow
fjords (Holtan 1976).
Phosphorus removal by chemical precipitation has been refined in Norway, Sweden
and Finland over the last 30 years. The concentration of phosphorus is easily reduced
down to 0,50 mg P/l in the effluent, measured as total phosphorus and a net removal
of 95 % or more is achieved. The cost and energy consumption in the chemical
precipitation process is low compared to biological P-removal methods, because
adding and mixing chemicals to the wastewater is far more energy efficient than the
aeration needed for biological treatment processes. Chemical precipitation also
removes other wastewater constituents than phosphorus (Table 1).
Table 1. Reduction of wastewater constituents other than phosphorus by chemical
precipitation (Vråle and Olsen 1994).
Wastewater constituent
Removal %
! Organic matter expressed as BOD 7
75-80
! Suspended solids
85-90
! Dissolved organic
30-55
! Total nitrogen*
15-40
* If the sludge from a chemical treatment plant is digested and the sludge is dewatered and
the water is sent back to the inlet the percent removal of nitrogen is reduced to approximately
5 %.
The energy consumption for chemical precipitation in Norway is only 0,23 kWh/m3
treated water for larger treatment plants (Ødegaard 1992). Most of this energy
consumption is used for heating and ventilation of the buildings over the treatment
basins. For biological treatment (activated sludge with only 30 % phosphorus
removal) the energy use is in the order of 0,37 kWh/m3 (O`Brien, J.K. 1986) showing
that from an energy aspect chemical precipitation is more sustainable than a biological
process.
In: L. Seng (ed.) Proc. International conference on natural resources and environmental management
and environmetal safety and health. Kuching, Malaysia. November 27-29, 2007.
6
Nitrogen removal
Removal of nitrogen in Norway was triggered by The North Sea Agreement in 1988.
For countries having direct discharge to the ocean, it is believed that nitrogen is the
main limiting factor for algae growth in the marine environment. According to the
North Sea Treaty, countries bordering the North Sea have agreed to reduce the input
of nutrients (nitrogen and phosphorus) by 50 % within year 2005, using emissions in
1985 as a baseline (SFT 1991).
Nitrogen removal is performed mostly by biological methods in large scale treatment
systems. Adding a nitrogen removal step with pre- or post-denitrification more than
doubles the energy consumption of the treatment plant if the original plant is based on
chemical precipitation. At the Lillehammer wastewater treatment plant (Table 2)
adding nitrogen removal increased the energy use by a total of 2,2 million kWh per
year or by additional 0,23 kWh/m3 (Moen and Lien 2000).
In Norway nitrogen removal has been a challenge due to low wastewater temperatures
in the winter and a very dilute sewage because of combined sewers and infiltration
water.
Two methods of nitrogen removal have been developed with success in Norway;
1) the moving bed Kaldnes system (KMTTM) and 2) the fixed bed biological filter by
Degremont. The latter process has been improved based on new types of expanded
clay aggregates (Filtralite HCTM and -HRTM) developed by Maxit of Norway.
Table 2. The major treatment plants with nitrogen removal in Norway (Moen and
Lien 2000).
Treatment
plant
Start of
N-
removal
Qdim
m3/h
Treatment process
before
N-removal
N-removal
process
Lillehammer
1994
1200
Mechanical/chemical
KMT pre and post
denitrification
VEAS Oslo
1993/95
6m3/s
Mechanical/chemical
DegrŽmont
/Maxitc and
ammonia stripping
Groos
1995
750
Pre-sedimentation
Activated sludge
biological P and N-
removal
N. Follo
1997
1125
Mechanical/chemical
KMT pre and post
denitrification
Gardermoen
1998
1300
Mechanical/chemical
KMT pre and post
denitrification
Bekkelaget
Oslo
2001
3m3/s
Mechanical/chemical
Activated sludge
pre-denitrification
All the plants except Groos uses a mechanical/chemical precipitation process prior to
the N-removal process. The table shows that 5 out of 6 plants for nitrogen removal
built in Norway have found it most economical and efficient to use a chemical
precipitation process in front of the N-removal process step. All the treatment plants
have had individual investigations before decisions have been made.
The reason for this combination, is that large amounts of organic matter and some
particulate nitrogen are coprecipitated with the phosphorus (Table 1). This reduction
In: L. Seng (ed.) Proc. International conference on natural resources and environmental management
and environmetal safety and health. Kuching, Malaysia. November 27-29, 2007.
7
reduces the needed areas and volumes for the nitrification and denitrification, and
gives an overall more efficient and economic process.
The Groos and Bekkelaget plants are based on an activated sludge process more
typical for the plants in Denmark and continental Europe. Based on a general
evaluation of the process these plants seem to be less sustainable at least from an
energy aspect.
New nitrogen removal processes
The KMTTM process
The KMTTM system is the most frequently used system (Table 2 and Fig. 1). The
KMTTM system uses three plastic biomedia with a specific surface area from 310–500
m2/m3. The biomedia enhances the efficiency of the system so that smaller volumes
are needed compared to a traditional activated sludge process, thus the energy process
is also improved. Other advantages are robustness to load variations and low
sensitivity to the tank shape and flexibility to operation.
Aerobic reactor Anoxic reactor
Fig 1. The Kaldnes process (principle) in a nitrification denitrification system. The
tanks are filled approximately 67% with biomedia. The media is kept moving by air
diffusers in the aerobic stage and by a mixer in the anaerobic stage.
The plants have a requirement to remove 70 % of the total nitrogen and this is
normally achieved.
The Degremont/Maxit process using FiltraliteTM
The VEAS plant is the largest in Norway and is based on the Degremont process for
N-removal (Sagberg and Berg 1999 a). There are 24 upflow nitrification filters each
with a surface 87 m2 and the media depth of 4 m. The biofilter consists of crushed
expanded clay aggregates developed in collaboration with the French company
Degremont and the Norwegian company Optiroc. The aggregate size is 3-6 mm. The
surface area of the round FiltraliteHR media is 3000-5000 m2/m3, which is larger than
for the KMT plastic biomedia. The crushed FiltraliteHC exposes the inner surface of
In: L. Seng (ed.) Proc. International conference on natural resources and environmental management
and environmetal safety and health. Kuching, Malaysia. November 27-29, 2007.
8
the porous aggregates and increases the available surface for biofilm development
compared to round or uncrushed aggregates.
At the bottom of the filters, heterotrophs degrade the carbonacious material. The
amount of carbon oxidized is this way only 9 % of the inlet carbon amount. In the
upper parts of the nitrification filters, the pH can drop as far down as to pH 5,5 at
temperatures down to 6 °C (Sagberg and Berg 1999a). The capacity of the
nitrification process is mainly oxygen limited.
After nitrification the water enters an upstream denitrification filter each having a
surface of 65 m2 and a total of 24 filters. The filtermedia has a depth of 3 m of 2,5-6
mm expanded clay aggregates. A carbon source is added to the water before it enters
the denitrification filter. The denitrification operates well at temperatures down to
10°C. At lower temperatures it is necessary to add small amounts of phosphoric acid
to maintain high rates of denitrification. This may also be necessary for the KMT
process, especially when post denitrification is used.
The overall removal of total-N at VEAS is 74 %; of this 61 % is removed as nitrogen
gas, 22 % is removed with the dewatered sludge (biosolids) and 17 % is removed as
adsorbed nitrogen from ammonia stripping (Sagberg and Berg 1999 a).
Ammonia stripping from filtrate water
The VEAS plant has built a closed loop ammonia stripping system, treating the
effluent from the sludge dewatering unit. The sludge from the digesters is
conditioned with lime before dewatering to rise the pH. The increase in pH results in
free ammonia, which is absorbed using nitric acid in an adsorption tower trapping the
ammonia rich air. The result is a 55 % solution of ammonium nitrate. The ammonium
nitrate is sold to a factory producing mineral fertilizer.
The cost efficiency of the ammonia stripping process, is described by Sagberg and
Berg (1999 b). This study concluded that the closed loop ammonia stripping from
filtrate water gives significant savings including capital costs at normal methanol
prices. It was also demonstrated that a duplication of the stripping facility, under
slightly higher methanol prices than historical average, would also be cost efficient
and probably one of the first choices if the N-removal capacity of the plant should be
increased.
Ammonia stripping is thus an interesting method from a sustainability aspect because
recycling of nitrogen is possible. However, ammonia stripping is to this date only
used in small scale and laboratory systems and not as the main N-removal method.
Investigations by Vråle (1992) showed very promising results, but ammonia stripping
has not been used in large scale applications due to fear of practical problems when
upscaling. At VEAS ammonia stripping is used in a sidestream and has not given
problems with scaling (Sagberg and Berg 1999 b).
SOURCE SEPARATING - RECYCLING SYSTEMS
Blackwater (toilet wastewater) contains , 90% of the nitrogen, 74% of the phosphorus,
79% of the potassium (Vinnerås 2002). In addition 30–75 % of the organic matter in
In: L. Seng (ed.) Proc. International conference on natural resources and environmental management
and environmetal safety and health. Kuching, Malaysia. November 27-29, 2007.
9
the wastewater is in the toilet waste (Jenssen and Skjelhaugen 1994). By the use of
urine separating, composting, or extremely water saving toilets, nutrients can be
collected and recycling facilitated (Jenssen 1999). Urine is an excellent fertilizer and
needs only 6 months of storage to obtain hygienic safety for agricultural use (Höglund
2001, Johansson et al. 2001). Concentrated toilet and organic household waste can
also produce energy via aerobic or anaerobic processes (Jenssen et al. 2003). In
Norway the main focus has been on the use of extreme water saving (e.g. vacuum)
and composting toilets. Substantial efforts are also devoted to the development of
simple greywater treatment systems as wetlands, biofilters or soil infiltration systems
or a combination of such.
Greywater treatment is an important part of a complete ecological sanitation system.
Greywater treatment options were considered by Rasmussen et al. (1996). In Norway
greywater treatment systems using simple LWA biofilter systems or a combination of
LWA biofilters and subsurface flow LWA constructed wetlands have been developed
(Jenssen and Krogstad 2001, Jenssen and Vråle 2004). The principle of a source
separating fully recycling system is shown in Fig. 2.
Figure 2. A fully recycling system using separate treatment of blackwater and
greywater. Blackwater from watersaving toilets (e.g. vacuum) is collected and treated
together with organic household waste.
Treatment and recycling of blackwater and organic waste
Vacuum and gravity operated toilets using 0,5-1,5 liter per flush are commercially
available. Using these toilets experience shows that 5-7 liters of blackwater is
produced per person and day (Gulbrandsen 1999). Using conventional flush toilets
the daily per capita production of blackwater would be 6–15 times higher. Using a
one liter toilet an average Norwegian family would produce 6-9 m3 blackwater per
year and 15 families would produce about 10 m3 of blackwater per month. Such
In: L. Seng (ed.) Proc. International conference on natural resources and environmental management
and environmetal safety and health. Kuching, Malaysia. November 27-29, 2007.
10
volumes are possible to handle separate. Even when the amount of flushwater is only
1 liter the dry matter content (DM) is usually below 1 %. In order to treat the
blackwater successfully by liquid composting, which is the most common process in
Norway, organic matter must be added (Jenssen and Skjelhaugen 1994). Grinded
organic household waste, animal manure or residues from various food processing
industries are all additives that bring the DM content up to a level where the
composting process is successful. An energy efficient liquid composting unit is
developed (Jenssen and Skjelhaugen 1994). The effluent from the liquid composting
unit is hygienized and odorless. The unit is running with a positive energy balance if
the heat generated by the composting process is utilized.
Anaerobic treatment in small, decentralized units has been considered uneconomical
in Norway. This is partly due to safety regulations, but also the climate that demands
better insulation and more sophisticated systems than in warm climates. Nevertheless
anaerobic processes are attractive due to the energy quality of gas being superior to
heat and less energy is needed to operate an anaerobic process. Work has therefore
started investigating the use of small-scale anaerobic reactors for cold climates.
A special direct ground injection system (DGI) was developed for injection of liquid
organic fertilizers (Morken 1998). This equipment does not penetrate the ground,
rather the fertilizer is injected under pressure. Immediate soil contact secures
ammonia adsorption and good plant accessability of the fertilizer. This reduces the
ammonia loss to 15–20 % as compared to traditional surface spreading methods
where the loss is 70–80 %. The equipment also makes it possible to sow at the same
time as the fertilizer is injected. The yields using injection of liquid organic fertilizer
compare well to conventional methods using mineral fertilizer.
Greywater treatment
Greywater contains minor amounts of nitrogen and phosphorus, but substantial
amounts of organic matter (Rasmussen et al. 1996). Indicator bacteria are present in
large numbers (Ottosen 2003). The need for treatment of the greywater depends upon
its final discharge or use. For discharge to the sea no or primary treatment is
sufficient. When the discharge is to inland lakes or rivers the authors recommend
secondary treatment. This may be achieved using a simple biofilter system. In order
to be able to discharge the greywater to small local streams or use it for irrigation or
groundwater recharge, reduction of the hygienic parameters as bacteria is important.
This can be obtained using a sand filter or a combination of a biofilter and a
subsurface flow constructed wetland (Fig 3 and Table 3). Biofilters and constructed
wetlands using lightweight expanded clay aggregates (LWA) or similar porous media
are pioneered in Norway (Jenssen et al. 2005).
A single pass biofilter aerates the wastewater and reduces oxygen demand (BOD) and
bacteria, thus, higher loading rates can be used for a subsequent infiltration system
(Heistad et al. 2001). The use of a single pass biofilter also provides new designs of
onsite natural systems (Fig. 3). In sloping terrain such filters can be operated by the
use of a siphon. Using such filters a 70 % BOD reduction and 2-5 log reduction of
indicator bacteria has been obtained at a loading rate for greywater of 115 cm/d.
Assuming a greywater production of 100 liters/person/day (Table 4) a biofilter of 1 m2
surface area can treat greywater from about 10 persons, hence, very compact biofilters
In: L. Seng (ed.) Proc. International conference on natural resources and environmental management
and environmetal safety and health. Kuching, Malaysia. November 27-29, 2007.
11
can be made. The key to successful operation of the biofilter is uniform distribution of
the liquid over the filter media and intermittent dosing (Fig. 3).
Figure 3. A soil infiltration system with pretreatment in a lightweight expanded clay
aggregate (LWA) biofilter (from Heistad et al. 2001).
For locations where traditional soil infiltration is not possible a simple biofilter alone
or a biofilter prior to soil infiltration or a constructed wetland system may be used
(Fig. 3 and 4). For cities a biofilter preceding a subsurface flow constructed wetland
has been used with success (Jenssen and Vråle 2004).
Figure 1. The latest generation of constructed wetlands for cold climate with
integrated aerobic biofilter in Norway (Jenssen and Vråle 2004).
For greywater a LWA biofilter/constructed wetland system can be designed very
compact (Jenssen and Vråle 2004, Jenssen 2005). With an integrated biofilter the total
surface area is 1-2 m2/person. This facilitates urban applications. The depth of the
The aerobic
biofilter with
domes
Horisontal
subsurface flow
constructed
wetland
Septic
tank
Pump/siphon
Level control
& sampling
port
In: L. Seng (ed.) Proc. International conference on natural resources and environmental management
and environmetal safety and health. Kuching, Malaysia. November 27-29, 2007.
12
wetland is minimum 1 meter and the biofilter 0,6 m. With this configuration very high
effluent quality is achieved (Table 3).
In Oslo the capital of Norway, greywater from 33 apartments (Klosterenga) is treated
to swimming water quality (Table 3) in the courtyard of the building (Jenssen 2005).
The area requirement for the total system is about 1 m2/person. The area covering the
biofilter is used as a playground. Additional aeration, in the summer, is provided by a
flowform system (Wilkes 1980). With effluent qualities as shown in Table 3 the need
for an elaborate secondary sewer system is reduced because local streams or water
bodies can be used for receiving the treated water.
Table 3 also shows effluent values for two other full scale greywater treatment
systems; one at the Agricultural University of Norway treating greywater from
student dormitories (Kaja) and the other treating greywater from 43 condominiums in
Bergen the second largest city in Norway (Torvetua). All three systems have the
same principal design as shown in Fig. 4.
Both the influent and the effluent values of these systems meet the WHO drinking
water standards with respect to nitrogen (<10 mg/l). The phosphorus concentrations
are also extremely low and the influent concentrations meet the Norwegian
requirement for small treatment plants that discharge to freshwater (< 1mg/l). The
reason for the low phosphorus influent concentrations are that phophate free
detergents are used in Norway. The TCB concentration in the GSTE is in the order of
104–106/100 ml.
Table 3. Greywater septic tank effluent (GSTE) and effluent values of three
biofilter/constructed wetland systems, average values (mg/l).
System
Built
year
Persons
served
BOD
GSTE
BOD
efflu-
ent
Tot-N
GSTE
Tot-N
efflu
-ent
Tot-P
GSTE
Tot-P
efflu-
ent
TCB**
efflu-
ent
Kaja
1997
48
88
6
8,8
2,4
1,0
0,1
<1000
Torvetua
1999
130
346*
44*
5,5
2,2
0,89
0,19
<100
Kloster-
enga
2000
100
ND
22*
ND
2,5
ND
0,02
<10
* COD, ** TCB=Termotolerant coliform bacteria (per 100 ml).
The bacteria concentration in the effluent (Table 3) meets the European standards for
bathing water (<1000 TCB/100 ml). All samples at Klosterenga, that utilizes the last
generation of the high phosphorus sorbing LWA termed Filtralite-PTM, have
consistently shown <10 TCB/100 ml. After treatment of greywater in a biofilter
followed by a constructed wetland the effluent can be discharged to local streams,
irrigation, or groundwater.
Water consumption
The traditional water toilet accounts for 20–40 % of the per capita water use (Gardner
1997). Table 4 shows that the per capita greywater production varies from 81 to 133
liters. The lowest greywater production displayed in Table 4 is from a Norwegian
ecovillage project and shows what is possible to achieve if the people are focused on
water conservation. At the student dormitories (Kaja) the greywater production is
higher despite water saving showerheads. Without water saving showerheads the
In: L. Seng (ed.) Proc. International conference on natural resources and environmental management
and environmetal safety and health. Kuching, Malaysia. November 27-29, 2007.
13
greywater production was 156 liters per student per day. This shows that the showers
account for a major part of the greywater production in the student dormitories. In
Norway young people (15–25 years) generally take more frequent and longer showers
than the rest of the population and thus it can be expected that the average greywater
production for the population as a whole is lower. Compared to the average normal
per capita water use in Norway the students at Kaja have a 27 % lower total water
consumption when they use vacuum toilets (1 liter/flush) and water saving
showerheads. The people of the ecovillage where composting toilets were used had a
50 % lower water use.
The excellent effluent quality (table 3) facilitates reuse of the water for irrigation,
groundwater recharge or for in-house applications. For flushing toilets and car wash it
may be possible to use the effluent water (tab. 3) without further treatment. However,
recent results show that greywater may contain virus and bacterial pathogens that are
not represented by the indicator bacteria (Ottosen and Stenström 2002). This may call
for further treatment before use as suggested above. In order to upgrade to drinking
water quality or for washing, microfiltration, reverse osmosis or carbon filtration may
be needed as a single step or in combination. If treated greywater is reused for in-
house applications more than 90% reduction in water consumption is possible.
Table 4. Water use in households liters/person and day.
Norway1
USA2
Ecovillage
Norway3
Kaja4
Blackwater
40
57
0
7
Greywater
120
133
81
112
Total
160
180
81
117
1 VrŒle 1987, 2 Crites and Tchobanoglous 1998, 3 Kristiansen and Skaarer 1979, 4 Søyland 1998.
Conclusions
Evaluation of sustainable wastewater treatment systems depends on a number of
factors, energy use and recycling beeing two essential parameters. Chemical
precipitation is more energy efficient than biological treatment methods and chemical
precipitation prior to nitrogen removal reduces both space and energy need for the
subsequent nitrogen removal step.
In Norway a moving bed reactor using plastic biomedia and a fixed film process using
expanded clay aggregates are the two main methods for nitrogen removal. Both
processes are robust and more efficient in terms of energy and space requirements
than activated sludge processes. However, recycling is not possible using these
biological methods. Ammonia stripping facilitates recycling, but is not yet developed
for application as the main nitrogen removal process in large treatment plants.
Experience from Norway shows that separate treatment of blackwater and greywater
nearly achieves "zero emission" and almost complete recycling. Organic household
waste can be treated in the same process as the blackwater and yield a fertilizer/soil
amendment and energy. The water consumption can be reduced by up to 50 % by
using water saving toilets and water saving fixtures and by > 90% if treated greywater
is recycled for in-house use. Compact, technically simple greywater treatment systems
In: L. Seng (ed.) Proc. International conference on natural resources and environmental management
and environmetal safety and health. Kuching, Malaysia. November 27-29, 2007.
14
facilitates decentralized treatment even in urban areas, thus the need for a secondary
piping and pumping system for transport of untreated wastewater is reduced.
References
Antonucci, P. C. and F. D. Schaumburg, Journ. of the Water Poll. Contr. Fed., 47(11),
pp 2694-2701 (1975).
Crites, R. and G. Tchobanoglous. 1998. Small and decentralized wastewater
management systems. Mc Graw-Hill, Boston.
Etnier, C. and P.D. Jenssen. 1997. The human waste resource in developing
countries: Examples of options for reuse of nutrients in agriculture and
aquaculture. Centre for International Environment and Development
Studies; Noragric, report 35. Agr. Univ. Norway.
Etnier, C. and B. Guterstam. 1991. Ecological engineering for wastewater treatment.
Proc. Int. Conf. Stensund, Bokskogen, Sweden.
Gardner, G. 1997. Recycling organic waste: From urban pollutant to farm resource.
Worldwatch Institute, paper 135, 58 p.
Graf, H. 2001. International Workshop on Assessment Methodologies for Urban
Infrastructure, Sept. 1999 Stockholm, Sweden.
Gulbrandsen, A. 1999. A watersaving vacuumsystem for transport of blackwater and
onsite treatment of greywater in a constructed wetland. M.Sc. Thesis. Dept.
of Engineering, Agr. Univ. Norway, s (In Norwegian).
Guterstam, B. 1991. Ecological Engineering for wastewater treatment : Theoretical
foundations and practical realities. In: C. Etnier and B. Guterstam (eds.)
Ecological engineering for wastewater treatment. Proc. Int. Conf. Stensund,
Bokskogen, Sweden pp. 38- 54.
Henze, M., L. Somyl—dy, W. Schilling and J. Tyson. 1997. Sustainable sanitation.
Wat. Sci. Tech. 35/9
Heistad, A., P.D. Jenssen and A.S. Frydenlund. 2001. A new combined distribution
and pretreatment unit for wastewater soil infiltration systems. In K. Mancl
(ed.) Onsite wastewater treatment. Proc. Ninth Int. Conf. On Individual and
Small Commmunity Sewage Systems, ASAE.
Holtan, H. 1976. Forurensningssituasjonen i Mj¿sa. Nivas rbok for 1976.
Höglund C (2001). Evaluation of microbial health risks associated with the reuse of
source separated human urine. PhD thesis, Department of Biotechnology,
Royal Institute of Technology, Stockholm, Sweden.
Jana, B.B., R.D. Banarjee, B. Guterstam and J. Heeb. 2000. Wasterecycling and
resource management in the developing world. Ecological engineering
approach. Univ of Kalyani, Kalyani India, Int. Ecol Eng Society, Wolhusen
Switzerland. ISBN 81-901208-0-8.
Jenssen, P.D. 1995. Natural systems technology for wastewater treatment. NAT-news
no1. Jordforsk, Aas, Norway.
Jenssen, P. D. 1999. An overview of source separating solutions for wastewater and
organic waste treatment. . In: Kløwe B et al. (eds.). Management the
wastewater resource. Proceeding s of the fourth international conference on
Ecological Engineering for Wastewater Treatment. Agricultural University
of Norway/Center for Soil and Environmental Research, Ås. June 7-11 1999.
Jenssen, P.D. and A. Vatn. 1991. “Ecologically sound wastewater treatment:
Concepts and implementation.” In: C. Etnier and B. Guterstam (eds.)
In: L. Seng (ed.) Proc. International conference on natural resources and environmental management
and environmetal safety and health. Kuching, Malaysia. November 27-29, 2007.
15
Ecological engineering for wastewater treatment. Proc. Int. Conf. Stensund,
Bokskogen, Sweden pp. 148-160.
Jenssen, P.D. and O.J. Skjelhaugen. 1994. Local ecological solutions for wastewater
and organic waste treatment - a total concept for optimum reclamation and
recycling. Proc. Seventh International Symposium on Individual and Small
Community Sewage systems, Atlanta, ASAE 18-94, pp. 379 - 387.
Jenssen, P.D og T. Krogstad. 2002. Design of constructed wetlands using
phosphorus sorbing lightweight aggregate (LWA). In: Treatment wetlands in
cold climate, Mander Ü. and Jenssen, P.D. (eds.), Advances in Ecological
Sciences no. 11, pp. 259-272.
Jenssen, P.,D., P.H. Heyerdahl, W.S. Warner and J. Greatorex. Local recycling of
wastewater and organic waste - a step towards the zero emission.
Community. In: T.D. Lekkas (ed.) Proc. 8th International Conference
Environmental Science and Tecnology, Lemnos Island Greece, 8-10
september 2003.
Jenssen, P. D. and L. Vråle. 2004. Greywater treatment in combined
biofilter/constructed wetlands in cold climate In: C. Werner et al. (eds.).
Ecosan – closing the loop. Proc. 2nd int. symp. ecological sanitation, Lübeck
Apr. 7-11. 2003, GTZ, Germany, pp:875-881.
Jenssen. P.D. 2005. Decentralized urban greywater treatment at Klosterenga Oslo. In:
H. v. Bohemen (ed.) Ecological engineering-Bridging between ecology and
civil engineering, Æneas Technical Publishers, The Netherlands, pp 84-86.
Jenssen P.D., T. Mæhlum, T. Krogstad and Lasse Vråle. 2005. Treatment
Performance of Multistage Constructed Wetlands for Wastewater Treatment
in Cold Climate. Journal of Environmental Science and Health. Vol 40 (6-7)
1343-1353.
Johansson, M., H. Jönsson, C. Gruvberger, M. Dalemo and U. Sonesson 2001. Urine
separation – closing the nutrient cycle. Stockholm Water Company,
Stockholm. http:// stockholmvatten.se/pdf_arkiv/english/urinsep_eng.pdf
Kløwe, B., C. Etnier, P.D. Jenssen, T. Mæhlum. 1999. Management the wastewater
resource. Proceedings of the fourth international conference on Ecological
Engineering for Wastewater Treatment. Agr. Univ. Norway, Agricultural
University of Norway/Center for Soil and Environmental Research, Ås.
Krogstad, T., T. Sogn, Å. Asdal and A. Sæbø 2005. Influence on the sewage sludge
purification process on plant available phosphorus in soil. Ecol. Eng 25: 51-
60.
Kristiansen, R. and N. Skaarer. 1979. BOV-vannets mengde og sammensetning.
Vann no. 2, pp. 151-156.
Larsen, E. 2000. Oppfølging av et fullskala anlegg for separat behandling av
svartvann og gråvann, men vekt på gråvannsbehandling. M. Sc. Thesis, Dept.
of Engineering, Agr. Univ. Norway (in Norwegian).
Lindholm, O. and T. Nordeide. 2000. Relevance of some criteria for sustainability in a
project for disconnecting of storm runoff. Environmental Impact Assessment
Review vol 20 p.413-423. Year 2000.
Urban water 2001. Urban Water Progress Report 2001:4. Chalmers University of
Technology, Sweden, ISSN 1650-3791.
Moen, S.E. and O. Lien. 2000. Oppsummering av resultater og erfaringer fra fors¿k
og drift av nitrogenfjerning ved norske avl¿psrenseanlegg. NORVAR
In: L. Seng (ed.) Proc. International conference on natural resources and environmental management
and environmetal safety and health. Kuching, Malaysia. November 27-29, 2007.
16
Rapport 102-2000.
Morken, J. 1998. Direct ground injection - a novel method of slurry injection.
Landwards, winter 1998, pp. 4-7.
Mæhlum, T. 1998. Cold climate constructed wetlands:Aerobic pretreatment and
horizontal subsurface flow systems for domestic sewage and landfill leachate
purification. Doctor Scient. Thesis 1998:9. Agricultural Univ. of Norway,
Dept. of Agricultural Eng., Ås, Norway.
O`Brien, J.K. 1986. Alternative Methodes of Financing Energy Conservation
Projevts for Activated Sludge Systems. Published in Teatment Efficiency and
Energy Use in Activated Sludge Prosess Control. Ann Arbor Science 1986.
Ottosen, J. and T. A. Stenström. 2002. Faecal contamination of greywater and
associated microbial risks. Water Research, 37, 645-655.
Rasmussen, G., P.D. Jenssen and L. Westlie. 1996. Graywater treatment options. In:
J. Staudenmann, et al. ed. Recycling the resource: Proceedings of the second
international conference on ecological engineering for wastewater treatment,
Waedenswil, Switzerland, Sept. 18-22 1995. Transtec, pp. 215-220.
Sagberg, P. and K.G. Berg. 1999 a. A compact N- and P-removal process at VEAS,
Norway. Presentation at a Nordic conference on nitrogen removal. Oslo. 2. -
4. Feb.1999.
Sagberg, P. and K.G. Berg. 1999 b. Cost optimization of nitrogen removal in a
compact nitrogen and phosphorus WWTP. Proceedings of the 8th IAWQ
conference on Design, Operation and Economics of Large Wastewater
Treatment Plants 6-9 September 1999, Budapest.
SSA 2007. www.sustainable-sanitation-alliance.org
SFT 1991 Nordsj¿deklarasjonen. TA-781/1991. Oslo.
Søyland, E. 1998. Source separation of wastewater in in Kajaveien 15 -17. M.Sc.
Thesis. Dept. of Engineering, Agr. Univ Norway, s (In Norwegian).
Staudenmann J., et al. 1996. Recycling the resource: Proceedings of the second
international conference on ecological engineering for wastewater treatment,
Waedenswil, Switzerland. Env. Research vol. (5-6),Transtec publications.
Vråle, L. 1987. Forurensningsmodell for avl¿psvann fra boliger – bestemmel,se av
spesifikke tall. NIVA rapport VA-6/87, Norwegian Institute of Water
Research, Oslo.
Vråle, L. 1992. Solumstrand renseanlegg. Nitrogenreduksjon med kombinert
kalkfelling og ammoiakkstripping i lukket anlegg. VideregŒende
unders¿kelser februar, mars og april 1992. CHK rapport A1711/92-144.
Vråle, L. and Olsen, R. 1994. Nitrogenfjerning i Drammensregionen. Sluttrapport.
Milj¿vernavdelingen, Fylkesmannen i Buskerud.
Zhu T. 1998. Phosphorus and nitrogen remov al in lightweight aggregate (LWA)
constructed wetland and intermittent filter systems. Doctor Scient. Thesis.
1997:16 Agricultural Univ. of Norway, Dept. of Agricultural Eng., s,
Norway.
Vinnerås, B. 2002. Possibilities for sustainable nutrient recycling by faecal separation
combined with urine diversion. Agraria 353 - Doctoral thesis. Swedish
University of Agricultural Sciences, Uppsala.
Werner C, Avendano V., Demsat S., Eicher I., Hernandes L., Jung C., Kraus S.,
Lacayo I., Neupane K., Rabiega A., Wafler M., 2004. Ecosan – closing the
loop. Proc. 2nd. Int Symp. Ecological Sanitation Lübeck Apr. 7-11, 2003.
GTZ Echborn Germany, 1004p. ISBN 3-00-012791-7.
In: L. Seng (ed.) Proc. International conference on natural resources and environmental management
and environmetal safety and health. Kuching, Malaysia. November 27-29, 2007.
17
Wilkes, J. 1980. Som stšd for det levende – Virbela flowforms. Balder 18/19 pp. 6-
13, JŠrna Sweden.
Wolgast, M. 1992. Rena vatten: Omtankar i kretslopp. Creanom, Sweden, 187 p.
Ødegaard H. (ed.) 1991. Emerging technologies in wastewater treatment. Proceedings
Of the conference: Environment Northern Seas, Stavanger Norway 26-30
August. Stavanger Forum, Stavanger Norway.
Ødegaard H. 1992. Fjerning av n¾ringsstoffer ved rensing av avl¿psvann. Tapir
forlag juli 1992.
... Although these processes have served well in meeting the respective discharge standards, they are energy-and resource intensive . Most of these processes were developed in the 1900s specifically to meet discharge standards through destructive removal of the pollutants, with little regard to their energy-intensity, carbon-footprint, or lifecycle impacts (US EPA, 2014); their immediate direct benefits of improved sanitation and ecosystem services were valued to be much greater (GYOBU et al., 2015;Jenssen et al., 2007;Lazarova et al., 2012;Soda et al., 2013Soda et al., , 2010. Current realizations and concerns about greenhouse gas emissions, natural resource depletion, sustainability, and affordability of sewage treatment technologies and the potential for recovering resources inherent in sewage have been driving the development of improved or alternate technologies for sewage management McCarty et al., 2011;Puyol et al., 2017;Shoener et al., 2014). ...
... In a similar vein, municipal sewage is now being viewed not just as a waste stream that has to be treated for disposal, but as a locally available, renewable resource from which reusable water, greener fuels and fertilizers, and other valuable commodities could be recovered for beneficial use (Hern andez-Sancho et al., 2015;Jenssen et al., 2007;Puyol et al., 2017;Van Der Hoek et al., 2016). Currently, the following three pathways have emerged as the feasible ones for recovering resources from sewage (Mo and Zhang, 2012): (i) anaerobic digestion of primary and secondary sludges for recovering energy content of sewage as heat and electrical energy; (ii) land application of the digested sludge to utilize their nutrient content as fertilizers; and (iii) reuse of the treated effluent in nonpotable applications. ...
Chapter
An integrated sewage treatment and resource recovery (STaRR) system is proposed as a greener alternative to the current practice where valuable components in the sewage are destructively removed at the expense of significant energy input. The STaRR system entails mixotrophic cultivation of algal biomass in primary effluent, followed by hydrothermal liquefaction (HTL) of the resulting biomass to recover its energy- and nutrient contents. Historically, photoautotrophic algal systems have been engineered for sewage treatment, either as a dedicated process for nutrient removal from secondary effluent or as a coprocess in concert with heterotrophic bacteria for organics and nutrient removal. In contrast, the STaRR system utilizes a novel mixotrophic algal strain that affords reduction of biochemical oxygen demand, nutrients, bacteria of concern, and viruses in sewage in a single step to yield discharge-ready effluent. Results from pilot scale field demonstration of the STaRR system at a local sewage treatment facility are presented documenting its performance in treating primary effluent to better than secondary treatment levels, and in recovering high percentage of its nutrient content. Reductions of bacteria and virus indicators by the STaRR system are found to be superior to those in a parallel secondary system. Higher heating value (HHV) of the algal biomass cultivated in the STaRR system averaged 24.2 MJ/kg. HTL of this algal biomass resulted in light biocrude yield of 5.4–10.8 dry wt% and heavy biocrude yield of 5.8–7.8 dry wt%. HHV of the resulting biocrude averaged 37.6 MJ/kg. The STaRR system on average recovered 70% of phosphate and 51% of nitrogen from the primary effluent, yielding 1.62 kg struvite, 0.34 kg calcium phosphate, and 3.92 kg ammonium sulfate per 100 m³ of primary effluent.
... Environmental sustainability goals focused on the preservation and efficient use of environmental resources. Sustainable wastewater systems aimed to reduce water, chemicals , and energy used in treatment (Bakir, 2001; Balkema, Preisig, Otterpohl, & Lambert, 2002; Jenssen et al., 2007; Otterpohl et al., 1997). As a result, treated wastewater was less Urban Geography 807 toxic and became a resource rather than a problem. ...
... As a result, treated wastewater was less Urban Geography 807 toxic and became a resource rather than a problem. Natural treatment systems maximized reuse options and retained nutrients by recycling sludge as compost and/or using treated wastewater to irrigate agricultural and other green areas (Flores et al., 2009; Jenssen et al., 2007; Otterpohl et al., 1997). Wastewater treatment solutions that were categorized as increasing social sustainability were those that satisfied basic human needs and were socially equitable. ...
Article
Rapid, unregulated urbanization in Tijuana, Mexico outpaces the city’s wastewater treatment capacity. Efforts to incorporate water reclamation and resource recovery technologies into the city’s treatment network present an opportunity to improve regional public and environmental health without relying solely on the region’s limited water resources. I compare two sustainable wastewater treatment technologies used in Tijuana to better understand their contributions to the city’s attempts to increase economic, social, and environmental sustainability. A sustainable indicator analysis reveals that both facilities utilize water reuse technologies and support reforestation programs. While the smaller-scale, alternative plant makes important contributions to reforestation, slope stabilization, and community education programs, it lacks the capacity and treatment standards of the large-scale, centralized plant to meet the current and future needs of Tijuana. However, I argue that if the final water quality produced by smaller-scale, alternative technologies can be improved, these types of facilities have the potential to augment larger-scale treatment plants and provide important, localized sustainability benefits in a transborder context.
... So far, the decision making of such projects is based on factors like capital costs, operating costs, and adaptability of technology under local conditions (Mahgoub et al. 2010). However, to develop sustainable wastewater treatment, it is required to view the treatment systems using a holistic approach (Jenssen et al. 2007). Therefore, besides the factors mentioned above, energy and environmental aspects are also essential to consider when deciding a treatment system. ...
Article
This article presents an environmental and energy analysis of a wastewater treatment plant operating on sequential batch reactor technology. The analysis of energy consumption shows that the electrical, mechanical, chemical, and human energy consumption works out to 0.26 kW h/m3 of the treated wastewater. The overall share of electrical energy consumption is 84%, and 15% share is of mechanical energy. Nearly 78% of the electrical energy is consumed in the aeration process. The biological oxygen demand, chemical oxygen demand, total suspended solids, total nitrogen, and total phosphorous are measured for the influent and effluent of the treatment plant. A reduction of 76–97% occurs in these parameters due to wastewater treatment. The greenhouse gas emissions arising directly from the treatment processes and indirectly from the electricity and diesel usage are estimated. The direct and indirect emissions from the wastewater treatment plant amount to 105 tCO2e/year and 1316 tCO2e/year, respectively. A projection of methane accumulation in the atmosphere from this plant till the year 2041 is also made. The contribution of this plant to the atmospheric accumulation of CH4 is projected to reach 8679 kg in 2029. The projection for 2030 and thereafter is 9468 kg. Analysis of the energy, environment, and wastewater treatment nexus is of significance to have a holistic view for the sustainable development.
... To fulfill this mandate, POTWs have relied on multiple processes, each requiring its own hydraulic residence time (HRT) in a dedicated reactor (Metcalf et al., 2013). Although these processes have served well in meeting discharge standards and protecting public health and receiving water quality, their energy-and resource-footprints and life-cycle impacts have now been a concern (Jenssen et al., 2007). Potential for formation of harmful byproducts during effluent disinfection is now recognized as an additional concern (Krasner et al., 2009). ...
Article
Today's wastewater utilities are facing the dilemma of balancing pathological threats of bacteria and viruses in their effluent against health threats associated with the byproducts of disinfection. A possible solution to this dilemma is to adopt secondary treatment technologies capable of concurrent pathogen reduction, minimizing the demand for external disinfectants. Towards this end, bacterial and viral reductions possible in algal wastewater treatment (WWT) systems are highlighted here and compared with those in conventional activated sludge (AS) systems and membrane bioreactor (MBR) systems. High log reduction values (LRV) of E. coli [>5] and fecal coliform [>7] have been achieved without any external disinfectants in the classical photoautotrophic algal WWT systems and in an emerging mixotrophic algal WWT system. LRVs of E. coli, fecal coliform, and somatic coliphages in the mixotrophic system are higher than those in AS systems and, comparable to those in MBRs. But, LRVs of F-specific coliphages, Enterovirus and Norovirus GI are greater in MBRs than in the mixotrophic and AS systems. The low-energy algal WWT systems providing high inherent reductions of bacteria and viruses can serve as affordable alternatives to the capital- and energy-intensive AS and MBR systems for greener WWT, meeting several of the United Nation's Sustainable Development Goals.
... Although effective in their respective removals, these processes are energy-and resource-intensive [2]. Most of these processes were developed in the 1900s, with little regard to their carbon-footprint or life-cycle impacts [3]; their benefits of improved sanitation and ecosystem services were valued to be much greater [4]. ...
Article
Photoautotrophic algal systems have been investigated as potentially greener and more sustainable alternatives to the traditional bacteria-based wastewater treatment (WWT) systems. This paper presents mixotrophic algal systems as better suited for WWT. Since the literature is void of mixotrophic WWT systems, a brief review of the laboratory results from the literature comparing the different types of algal metabolisms is presented first. Details of a mixotrophic WWT system driven by an extremophilic alga, Galdieria sulphuraria (pH = 1 to 4; temperature = 25 to 56 °C) are presented next. Results from pilot scale version of this mixotrophic system (700 L) are summarized to show that it can reduce biochemical oxygen demand (BOD) and nutrients in primary-settled wastewater in a single step to yield discharge-ready effluent in < 3 days of fed-batch processing. Average volumetric removal rates of BOD 5 (16.5 ± 3.6 mg L −1 d −1) and ammoniacal nitrogen (6.09 ± 0.92 mg L −1 d −1) in this mixotrophic system were found to be not different from those reported for the photoautotrophic high rate algal ponds (significance level of 0.05); but, that of phosphates (1.40 ± 0.57 mg L −1 d −1) is greater than that reported for the photoautotrophic high rate algal ponds (significance level of 0.05). Additionally, the extreme culture conditions in this particular mixotrophic system enabled concurrent reductions of E. coli (> 5 log) and other pathogenic bacteria.
... Recycled sludge liquid from anaerobic digesters and separated collected urine are two wastewater streams of particular interest for nutrients recovery due to the high concentrations of nitrogen and phosphorus in relatively low flows. Percentages of nutrients present in chemical fertilizers that can be substituted by those recovered from wastewater vary and depend on several factors, one being whether a country has a net import or export of food [10]. In this way, Norway can substitute 15%–20% of its mineral fertilizer [11] while, according to Etnier and Jenssen [12], more than 40% of the nutrients present in chemical fertilizers could be substituted by nutrients recovered from wastewater in developing countries. ...
Article
Full-text available
A novel ammonia stripping method, including a CO 2 pre-stripper was used to treat a mix of supernatant liquor from an anaerobic digester and urine in order to recycle nitrogen as ammonium sulfate at full-scale in the WWTP Kloten/Opfikon. Waste streams were not generated, since the ammonia was recovered as a marketable nitrogen fertilizer, turning a waste product into a valuable product. The efficiency of this system was increased by means of the addition of pre-treated urine collected separately at EAWAG building. The separation step was performed by the use of water free urinals and urine diversion flush toilets. An increase of 10% in the liquid flux with the addition of the urine translated into a 40% increase of the ammonia concentration in the inlet of the stripping unit. The achievement of these percentages generated a proportional increase in the fertilizer production. The urine pre-treatment was carried out by adding magnesium to produce a precipitate of struvite. The first experiments with the combined treatment showed the feasibility of the combination of the separation and pre-treatment steps.
... The same estimation [10] reports a value of 30 kg/p.e.·y as for the COD load (data not included in the graph) whose distribution is 41% in greywater, 12% in urine and 47% in faeces which highlights the biological treatability of greywater while composting or biogas conversion would be the preferable fate of faeces, possibly joint with other biowastes. In developing countries more than 40% of the nutrients present in chemical fertilizers could, theoretically, be substituted with nutrients from wastewater [11]. The separation of these high loaded streams from domestic wastewater has several advantages in the operation of existing wastewater treatment plant (WWTP). ...
Conference Paper
Full-text available
Sanitation is meant to guarantee proper hygienic condition at household level and avoid the spreading of waterborne diseases. Conventional sanitation utilizes large flow of water as waste carrier (flush toilets) other than what is needed for food processing and hygiene. Such system is very costly both for the supply and the collection and treatment for disposal. Reuse and nutrient recovery is often hindered by the dilution and the contamination thus breaking the cycle of nutrients. It is unaffordable for countries with lack of water. An alternative approach is looked for by ecological sanitation based on systematic implementation of reuse and recycling of nutrients by separating at the source the different waste flows: those from washing operation and those from toilets. Moreover, faeces and urine could be collected separately with urine diverting toilets.
Article
Full-text available
Continuous population growth associated with sanitation, food waste (FW), and domestic wastewater (DWW) is becoming critical globally. Crucial efforts and appropriate measures to utilize the FW and DWW for resources are needed. This paper reviews the conventional treatment techniques, challenges, and associated merits for treating FW and DWW. In the context of this review, DWW is often referred to as blackwater (BW)/feces. Due to the rationale for resource amplification, the review proposed that both mixtures (FW and DWW) be stored in a sub-surface storage tank for several months or years. They are further biodegraded in a bioprocess to generate energy with stabilized digestates. The effluent’s peculiar features are low organic acids with a low pH4 value, offering a stabilized and sanitized effluent. The second proposed route was to integrate anaerobic digestion, composting, and pyrolysis. Anaerobic digestion will offer bioenergy and digestates. Composting will cater to compost production and avert digestate drying and heating costs during pyrolysis. The pyrolysis of the digestates will generate biochar and bioenergy materials, while improved bioprocess performance is attained with the simultaneous biochar utilization in the bioprocess. The integrated technological routes can valorize DWW and FW for maximum resource recovery and sustainable development in a real-world context. The concept can be applied to an existing facility to create a cleaner and more efficient DWW with FW recycling. However, a comprehensive techno-economic analysis must be conducted.
Article
Full-text available
This paper proposed a full-scale thermal sanitation and drying system for sewage sludge, powered by biogas and solar energy, from a small anaerobic sewage treatment plant. For that, the characterization of the investigated sewage treatment plant was carried out, determining the average monthly volumes of sludge, biogas, and methane available. Then, from small-scale experiments, the performance of two different configurations of the referred system was evaluated, with metallic and concrete underfloor heating. Three experimental campaigns with different sludge loads were carried out, varying the initial total solids content of the sludge (5 and 40%) and the thickness of the material deposited on the radiant floors (10 and 20 cm). The results obtained subsidized the choice of the configuration and the sludge load considered most favorable for the proposition in question, allowing the pre-dimensioning of the system for the treatment of about 211 m³ month⁻¹ of sludge, with 5% total solids. Thus, two radiant metal floors with 50 m² must be adapted, which must be loaded with sludge in a 10 cm layer, after their previous dewatering in drying beds (40% total solids). The temperatures reached made it possible to sanitize the material, as well as to increase the total solids content up to 75%. As solar energy is used, the estimated average consumption of methane is 11.363,19 Nm³ month⁻¹, a volume available at the sewage treatment plant and sufficient to process all the sludge generated there over 3 monthly cycles lasting 9 days. Keywords: sustainable SWTP; sludge heat treatment; sanitation and drying of sewage sludge; biogas; solar energy
Article
Wastewater treatment facilities typically transform nitrogen compounds into innocuous nitrogen. Phosphorous is partially recovered in biosolids while the potassium cycle in the treatment process is still not well mapped. This paper provides a mapping of the nutrients from household sources (urine, faeces and greywater) to wastewater in the traditional wastewater treatment plants. Following this mapping, the article critically reviews the nutrients recovery technologies, including their applicability at source (for urine) and centralised (for wastewater) levels, benchmarking, social acceptance, and techno-commercial assessments. Additionally, the paper has identified the current technological challenges and opportunities as well as suggested a several future recommendations for developing commercially viable nutrient recovery technologies from urine at source level and wastewater at wastewater treatment plants (centralised level). The high energy requirement, high cost and safety issues are some of the common challenges for most of the nutrient recovery technologies. However, anaerobic membrane bioreactor integrated with biochar or zeolite (for wastewater) and biosorption (for both urine and wastewater) can be highly attractive from those perspectives.
Conference Paper
Glacial till, often with poor hydraulic conductivity or a topography that limits the use of traditional wastewater soil infiltration systems (WSIS), is the dominant soil type in Norway. A newly developed combined distribution and pretreatment unit overcomes some of the soil limitations and extends the use of WSIS. The new system, which may be used in any soil type, allows easy access to the infiltrative surface and is thus superior to traditional gravel filled trenches regarding monitoring and maintenance of WSIS. The new system is based on high head pumping of septic tank effluent to one or several units filled with lightweight clay aggregates (LWA). Each unit is directly connected to the pump by a small diameter pipe, and one small pump can serve several units. The wastewater is dosed through a single tangential/fullconical (TF)-nozzle that distributes the water evenly over the 2.3m 2 surface of the pretreatment filter. The filter medium can easily be replaced, and the nozzle can be refitted by hand. The wastewater is distributed to the different units using a hydrosplitter, or for larger or more advanced systems, using solenoid valves controlled by a timer or a programmable logic controller (PLC). The use of a PLC makes individual loading rates and dosing frequencies possible. It is also possible to adjust the loading to soil moisture conditions or groundwater levels beneath or adjacent to the unit. The even distribution assures good utilization of the LWA filter media, and a significant reduction in BOD, SS, number of coliforms as well as nitrification is achieved. Higher soil acceptance rates for wastewater are therfore possible.
Article
This paper evaluates the relevance of different methods and criteria for choosing the best technical system to solve a combined sewer overflow problem in a catchment in Oslo. Two systems are evaluated; namely conventional, or nature based. A discussion of different criteria and rough numerical calculation of these are done. It is shown that the nature-based alternative has the best sustainability with a good degree of robustness. The LCA method was found to be too comprehensive and complicated in the present situation, compared to the benefits one will get. A simple EIA analysis with a pragmatic choice of criteria was found most suitable.
Article
Based on overall mass balances for water, total nitrogen and organic carbon in the VEAS WWTP in 1997, alternative strategies for nitrogen removal are discussed based on cost optimisation. Marginal costs for biological removal are compared with total costs for side stream treatment by ammonia stripping. If the plant has sufficient capacity to meet the effluent requirements with biological removal alone, this study demonstrates that the price of methanol determines whether or not invetment in ammonia stripping still is a cost efficient solution. Keywords Ammonia stripping; biofilm nitrogen removal; chemical pre-precipitation; compact N and P removal; cost efficiencies; mass balances Vestfjorden Avløpsselskap (VEAS), located outside Oslo, Norway, has a WWTP serving some 450,000 persons. The plant is located inside rock caverns. The plant is unstaffed more than 70% of the time, run by computers. Originally, VEAS was a direct precipitation plant for phosphorus removal with three hours retention time. In the period 1991-1997, the plant was rebuilt into a nitrogen and phosphorus removal facility, without extending the surface area of the plant. The goal for the new process was to remove 70% nitrogen and 95% phosphorus on a yearly basis. The concept was developed by VEAS, with the goal of keeping the process as compact as posi- ble within the existing area. The total retention time of the water in the process is only three
Article
The faecal contamination of greywater in a local treatment system at Vibyåsen, north of Stockholm, Sweden was quantified using faecal indicator bacteria and chemical biomarkers. Bacterial indicator densities overestimated the faecal load by 100-1000-fold when compared to chemical biomarkers. Based on measured levels of coprostanol, the faecal load was estimated to be 0.04 g person(-1) day(-1). Prevalence of pathogens in the population and the faecal load were used to form the basis of a screening-level quantitative microbial risk assessment (QMRA) that was undertaken for rotavirus, Salmonella typhimurium, Campylobacter jejuni, Giardia lamblia and Cryptosporidium parvum. The different exposure scenarios simulated--direct contact, irrigation of sport fields and groundwater recharge--gave unacceptably high rotavirus risks (0.04 < Pinf < 0.60) despite a low faecal load. The poor reduction of somatic coliphages, which were used as a virus model, in the treatment was one main reason and additional treatment of the greywater is suggested. Somatic coliphages can under extreme circumstances replicate in the wastewater treatment system and thereby underestimate the virus reduction. An alternative QMRA method based on faecal enterococci densities estimated similar risks as for rotavirus. Growth conditions for Salmonella in greywater sediments were also investigated and risk modelling based on replication in the system increased the probability of infection from Salmonella 1000-fold, but it was still lower than the risk of a rotavirus infection.
Univ Norway, ?s (In Norwegian) Recycling the resourceTranstec publications
  • Thesis
  • Dept
  • Engineering
  • Agr
  • J Staudenmann
Thesis. Dept. of Engineering, Agr. Univ Norway, ?s (In Norwegian). Staudenmann J., et al. 1996. Recycling the resource: Proceedings of the second international conference on ecological engineering for wastewater treatment, Waedenswil, Switzerland. Env. Research vol. (5-6),Transtec publications
Direct ground injection - a novel method of slurry injection
  • J Morken
Morken, J. 1998. Direct ground injection - a novel method of slurry injection. Landwards, winter 1998, pp. 4-7
Treatment Performance of Multistage Constructed Wetlands for Wastewater Treatment in Cold Climate
  • P D Jenssen
  • T Mæhlum
  • T Krogstad
  • Lasse Vråle
Jenssen P.D., T. Mæhlum, T. Krogstad and Lasse Vråle. 2005. Treatment Performance of Multistage Constructed Wetlands for Wastewater Treatment in Cold Climate. Journal of Environmental Science and Health. Vol 40 (6-7) 1343-1353