Annexes to COM(2000)469 - Green Paper - Environmental issues of PVC - Main contents
Please note
This page contains a limited version of this dossier in the EU Monitor.
| dossier | COM(2000)469 - Green Paper - Environmental issues of PVC. |
|---|---|
| document | COM(2000)469  |
| date | July 26, 2000 |
The success of this approach will require a constant progression in the efforts realised in the specific areas covered by the agreement and, in particular, reduction in the production and use of certain additives, more ambitious target quantities for recycling, industry's contribution to added costs of incineration, and a fully operational funding mechanism.
As regards cadmium, industry has committed itself to phase out the use of cadmium stabilisers in 2001. This commitment does not cover the imports of PVC from third countries, which might still contain cadmium.
Concerning the use of lead, the European Stabilisers Producers Association (ESPA) has committed itself to carry out "initial risk assessments on lead-based stabilisers under the CEFIC and ICCA [37] programmes 'confidence in chemicals' by 2004".
[37] CEFIC: European Chemical Industry Council ICCA: International Council of Chemical Associations
ESPA has committed itself to produce yearly statistics showing which stabilisers are purchased by converters. ESPA anticipates that the 120,000 tonnes of lead used in PVC in 1999 will decrease to 80,000 tonnes in 2010 and has stated that it "will support this trend by developing suitable alternatives". The PVC stabiliser industry does not at present take measures to phase out the use of lead in PVC, other than to "continue to research and develop alternative stabilisers to the lead-based systems".
Issues for consideration
The Commission considers, on the basis of the above-mentioned analysis, that the contamination of the environment by lead and cadmium should be avoided as much as possible. The Commission is in favour of a reduction of the use of cadmium and lead as stabilisers in PVC products. A number of measures could be envisaged and should be assessed in the light of their potential environmental and economic implications.
1. Legislative phase-out or other risk reduction measures for cadmium and/or lead with the possibility of temporary derogations
2. Implementation of the voluntary commitment of the PVC industry on cadmium
3. Development of further voluntary commitments for lead.
Question n°1: Which set of measures should be implemented to address the issue of the use of lead and cadmium in new PVC- According to which timeframe-
3.3. Plasticisers
Plasticisers are necessary to manufacture flexible PVC products. In Western Europe about one million tonnes of phthalates are produced each year, of which approximately 900,000 tonnes are used to plasticise PVC. In 1997, 93% of the PVC plasticisers were phthalates. The most common phthalates are: bis-2-ethylhexyl phthalate (DEHP), diisodecyl phthalate (DIDP) and diisononyl phthalate (DINP). In recent years the use of DEHP has decreased, while that of DIDP and DINP has increased. The quantities of plasticisers added to the PVC polymer vary depending on required properties. Depending on the final use, plasticiser contents vary between 15 and 60%, with typical ranges for most flexible applications around 35 to 40%.
Other plasticisers, in particular adipates, trimellitates, organophosphates and epoxidised soybean oil can also be used as softeners in PVC. These plasticisers represent only a small fraction of the use of plasticisers. Information on the impact of these plasticisers on the environment and on human health from their use in PVC is limited and further data would need to be acquired for a proper assessment. This section will therefore concentrate on phthalates, the most important plasticisers in term of quantity and the main plasticisers currently assessed in term of environmental and health risks.
Phthalates are high production volume chemicals, five of which have been put, due to their potential risks to human health and the environment, on the first three priority lists for risk assessment in accordance with Regulation 793/93 on existing substances. The risk assessments on these five substances are carried out by Member State rapporteurs [38]. The risk assessments on DEHP, DIDP, DINP, DBP have been or are expected to be completed in 2000 and in 2001 for BBP.
[38] The five phthalates are : Bis(2-ethylhexyl) phthalate (DEHP), rapporteur Sweden; Di-''isononyl''phthalate (DINP), rapporteur France; Di-''isodecyl''phthalate (DIDP), rapporteur France; Dibutylphthalate (DBP), rapporteur the Netherlands; Butyl Benzyl Phthalates (BBP), rapporteur Norway
DEHP, DINP and DIDP have a potential for bioaccumulation. The risk assessments under Regulation 793/93 have concluded that no concern exists for the accumulation potential of DBP, DINP and DIDP, whereas the potential effects on the environment are still being assessed for DEHP and BBP. Long-chain length phthalates have a low biodegradability under normal conditions of sewage treatment and are only partly degraded in usual leachate and sewage treatment plants, where they accumulate on suspended solids. Certain phthalates as well as their metabolites and degradation products can cause adverse effects on human health (in particular on liver and kidney for DINP and on testicles for DEHP). Potential endocrine disrupting properties are being evaluated.
All the phthalates used in large quantities in PVC applications are ubiquitous in the environment today. Transport in the air and leaching out from certain applications seem to be the major routes by which phthalates enter the environment. Phthalates are found in high concentrations mostly in sediments and in sewage sludge. In Denmark, it has been reported that the concentrations of certain phthalates can exceed the national limit values fixed for the use of sewage sludge in agriculture.
The risks due to the use of phthalates in certain soft PVC toys and childcare articles have been assessed by the Scientific Committee on Toxicity, Ecotoxicity and the Environment (CSTEE). Phthalates leach out from toys and child care articles, when sucked by small children. In its opinions, the Scientific Committee on Toxicity, Ecotoxicity and Environment has expressed its concern about the risks resulting from the exposure of small children to two phthalates (DINP and DEHP) used in these products, due to the potential adverse effects on liver, kidney and testicles. The Commission has adopted on 10 November 1999 a Proposal for a Directive and on 7 December 1999 a Decision under the emergency procedure of Directive 92/59/EC in order to ban of the use of phthalates in certain toys and childcare articles intended to be put in the mouth.
Without waiting for the final stage of the above mentioned risk assessment process, three Member States have already started to draw up risk management strategies based on the global objective to reduce the use of phthalates. The Swedish Government has presented a bill on "Swedish environmental quality objectives" which aims at reducing the use of the main phthalate DEHP [39]. The Danish government has adopted an action plan to reduce the use of phthalates by 50% over the next 10 years. The sustainability of flexible PVC has also been assessed by the German Umweltbundesamt [40], which recommends a phase-out of flexible PVC, for those applications where safer alternatives are available, due to the permanent loss of softeners, in particular phthalates, into the environment.
[39] The Swedish Government states that "the use of DEHP and other plasticizers with harmful effects in PVC for outdoor use in coated woven fabrics and coated plate and for corrosion protection in cars should be phased out on a voluntary basis by 2001. Other uses of DEHP as a plasticizer in PVC, with the exception of medical products and drugs, should be phased out on a voluntary basis by 2001."
[40] Deutsche Umweltbundesamt, Handlungsfelder und Kriterien für eine vorsorgende nachhaltige Stoffpolitik am Beispiel PVC, 1999
Issues for consideration
The use of phthalates in PVC applications raises issues, described above, which could be addressed through a number of measures, including legislative or voluntary risk reduction measures. These potential measures should be assessed in the light of their environmental and economic implications.
Question n°2: Should specific measures be taken for the use of phthalates as plasticisers in PVC- If so, when and through which instruments-
4. The waste management of PVC
Four studies have been commissioned by the services of the Commission in order to assess the technical aspects of the main waste management options for PVC waste: mechanical recycling [41], chemical recycling [42], incineration [43] and landfilling [44].
[41] Prognos, Mechanical recycling of PVC wastes, Study for DG XI, January 2000
[42] TNO, Chemical recycling of plastics waste (PVC and other resins), Study for DG III, December 1999
[43] Bertin Technologies, The influence of PVC on quantity and hazardousness of flue gas residues from incineration, Study for DG XI, April 2000
[44] Argus in association with University Rotstock, cit. op.
The management of PVC waste should be assessed in the context of the European waste management policy. The Communication from the Commission on the review of the Community strategy for waste management [45] has confirmed "the hierarchy of principles that prevention of waste shall remain the first priority, followed by recovery and finally by the safe disposal of waste". It is further stated that "preference should be given, where environmentally sound, to the recovery of material over energy recovery operations. This general rule is based on the fact that material recovery has a greater effect on waste prevention than energy recovery. It will nevertheless be necessary to take into account the environmental, economic, and scientific effects of either option. The evaluation of these effects could lead, in certain cases, to preference being given to the energy recovery option." In its Resolution [46] of 24 February 1997, the Council has endorsed this hierarchy of principles.
[45] COM(96) 399 final
[46] 97/C 76/01
4.1. Current situation and future developments
Current situation
The total quantity of PVC waste is a function of PVC consumption. However, due to lifespans, which can reach up to 50 years and more for some applications such as pipes and profiles, there is a "time-lag" between PVC consumption and PVC presence in the waste stream. PVC products reached significant market share in the 1960's. Considering lifespans of about 30 years and more, a significant increase of PVC waste quantities is expected to start around 2010.
Due to the fact that PVC is used in a wide range of applications, data on PVC waste arisings in the EU are uncertain. The most recent and detailed data available on PVC waste quantities are estimations carried out by industry and are based on calculations using production quantities per year and average lifespan of products.
It is estimated that in 1999 the total annual PVC waste quantity was about 4.1 million tonnes in the Community, which can be divided into 3.6 million tonnes of post-consumer PVC waste and 0.5 million tonnes of pre-consumer PVC waste. Pre-consumer wastes are generated during the production of intermediate and final PVC products as well as during the handling and installation of PVC products. The present composition of PVC waste is two thirds flexible PVC and one third rigid PVC.
About one million tonnes of PVC is present in the construction and demolition waste stream. One million tonnes of PVC can be found in the municipal solid waste stream, which comprises wastes collected from households as well as similar wastes collected from commercial and industrial operations. About 700,000 tonnes of PVC packaging waste are generated and about 700,000 tonnes of PVC are found in end of life vehicles and electrical and electronic equipment.
At present the main waste management route in the Community for all types of post-consumer waste is landfilling. This is therefore also the case for post-consumer PVC waste. About 2.6 to 2.9 million tonnes of PVC waste are currently landfilled every year. Mechanical recycling is applied to only a small fraction of the post-consumer waste (about 100,000 tonnes). Approximately 600,000 tonnes of PVC are incinerated per year in the Community.
Future developments: baseline scenario
This scenario [47] describes the situation with regard to the quantities of PVC waste and the main waste management routes expected in the years 2000, 2010 and 2020, with the assumption that no PVC-specific measures will be taken except for those legal, administrative and voluntary measures in force or in preparation at Community and at national levels. It is assumed under this scenario that existing and future Directives on landfilling, incineration, packaging, end of life vehicles and electric and electronic waste will be implemented.
[47] Prognos, cit. op.
The key element in the management of post-consumer PVC waste is the expected increase in PVC waste quantities. Predictions of future PVC waste arisings are subject to uncertainties but it is expected that the volume of PVC waste will increase significantly by 30% in 2010 and by 80% in 2020, in particular due to the important increase of waste quantities from long lifespan products. Post-consumer wastes will increase from about 3.6 million tonnes at present to about 4.7 million tonnes in 2010 and 6.2 million tonnes in 2020. PVC pre-consumer wastes will increase from 0.5 to 0.9 million tonnes.
Compared to the current situation, it is expected that the composition of PVC post-consumer waste arisings by product group will change. The share of PVC building waste and waste from household and commercial products will increase, whereas the contribution of packaging is expected to decrease significantly. The proportion of flexible PVC waste will also decrease.
In the context of the baseline PVC waste scenario, changes in waste management legislation and practices are expected to have the following effects:
* The landfill Directive will bring some important changes to waste management mainly due to the expected increasing landfill costs. Some Member States, in particular Germany, Austria, the Netherlands and Denmark have announced national policies for banning the landfilling of untreated organic wastes, including plastics, with the exception of PVC waste for Denmark.
* Recycling is expected to increase significantly over the next decades, in particular for those waste streams for which recycling targets will be set. Energy recovery is also expected to increase for waste, which cannot be recycled.
How this will affect the treatment of PVC waste will be discussed in more detail in the following sections on the main waste management options.
4.2. Mechanical recycling
Mechanical recycling refers to recycling processes where PVC waste is treated only mechanically, mainly through shredding, sieving, and grinding. The resulting recyclates (in powder form) can be processed into new products. Depending on the degree of contamination and the composition of the collected material, the quality of the PVC recyclates can vary a lot. The quality of the recyclates determines the degree, to which virgin material can be substituted by recyclates: "high-quality" recyclates can be re-used in the same types of PVC applications, whereas "low-quality" recyclates from mixed waste fractions can only be "down-cycled" into products usually made from other material.
Recycling of post-consumer waste is still at a low level in the EU and the quantities recycled represent less than 3% of the total [48]. About 100,000 tonnes are currently recycled per year in the EU. A major part of the post-consumer PVC waste recycling (about 70%) is down-cycling in the area of cable wastes (about 38,000 tonnes) and packaging waste (about 19,000 tonnes).
[48] Prognos, cit. op.
High-quality mechanical recycling for post-consumer wastes is still in a preliminary stage and exists only for few product groups and with low quantities (about 3.600 tonnes of rigid profiles, 5,500 tonnes of PVC pipes and 550 tonnes of flooring).
There appears to be no Member States where the recycling rate of post-consumer waste is significantly higher than the EU average. In some countries, collection schemes have been established, usually through voluntary approaches. However, the recycling rate is usually below 5% and is largely based on the down-cycling of packaging and cables.
As far as pre-consumer wastes are concerned, about 420,000 tonnes of PVC were recycled in 1998, representing about 85% of pre-consumer PVC waste arising. Mechanical recycling of pre-consumer waste exists in all Member States and can be considered as a profitable economic activity.
A number of life cycle assessments [49] on some specific PVC products have shown that mechanical recycling provides an environmental advantage for production waste, cut-offs and post-consumer PVC waste, which can be separated. The environmental advantages of the down-cycling of mixed plastics for the production of products which substitute concrete, wood or other non-plastic applications are less certain.
[49] Prognos, cit. op.
However, the presence of additives classified as hazardous, such as lead, cadmium and PCBs, in large PVC waste streams raises specific issues during their potential recycling. The recycling of PVC waste containing heavy metals results in a dilution of these substances in a greater quantity of PVC, since it is necessary to add virgin material. The heavy metals are not directly released into the environment during the recycling process and the renewed service life. The recycling of PVC material containing these heavy metals postpones the final disposal to a later stage. Although it could be difficult to control the use of recycled PVC containing lead and cadmium, for technical reasons it is unlikely that PVC waste from various applications would be recycled together in case of high quality recycling. Due to the product-specific additives formulations, recyclers would prefer recycling into similar applications. Additional measures, such as restrictions of the uncontrolled sale of recyclates containing heavy metals or its down-cycling, could be envisaged. A prohibition of the recycling of PVC waste containing heavy metals would eliminate the mechanical recycling of post-consumer PVC wastes from building applications - the waste stream with the highest potential for high-quality recycling - as they virtually all contain lead or cadmium. It should be noted that, except for Denmark, Member States, which have banned the use of cadmium as stabilisers, allow the recycling of PVC waste containing cadmium. The problem of PCBs in PVC cable waste has been addressed in Directive EC/96/59 on the disposal of PCB and PCT, which provides that cables containing more than 50 ppm of PCBs are considered as PCBs and have therefore to be decontaminated or disposed of in accordance with the provisions established under this Directive.
PVC can have a negative influence on the recycling of other plastics in mixed plastic waste. When PVC is processed with other plastics, such as in the packaging waste stream, the processing temperature is limited to the range of PVC-processing, which is a relatively low range compared to other plastics. Due to similar densities, polyethylene terephthalate (PET) and PVC waste are difficult to separate and the presence of PVC puts additional costs on some PET recycling schemes such as the PET bottles. In some cases, the PVC industry has recognised this issue and contributes to this additional cost.
As in the case of other materials, the recycling of PVC is also limited by the overall recycling costs. Economic profitability is reached when the net recycling costs (i.e. the overall costs for collection, separation and processing minus the revenues from sale of the recyclates) are lower than the prices for alternative waste management routes for related PVC wastes. If economic profitability cannot be reached, the recycling of PVC waste will not take place under free market conditions, unless there are legal obligations or voluntary measures enforcing or promoting the recycling of PVC. Collection represents the major bottleneck regarding the availability of waste and costs.
High-quality recycling of post-consumer waste (in particular pipes, profiles, flooring) is at present not profitable, as the net recycling costs are well above the costs for landfilling or incineration. In addition, there are further costs for the waste owner for separation of wastes at the construction sites.
Low-quality recycling of post-consumer PVC waste, such as for packaging waste, is not economically profitable. Economic profitability is not likely to be reached for other waste streams suitable for low-quality recycling, such as office supplies, printing films. Cable insulation is the only post-consumer waste, which can be recycled at competitive costs, due to the presence of valuable metals, such as copper.
In conclusion, the recycling of pre-consumer waste can, in principle, be profitable. However, post-consumer PVC waste recycling is far from reaching economic competitiveness. In addition to the establishment of recycling schemes with a broad regional coverage, financial incentives are necessary for a separate collection of PVC wastes. Also, PVC is often present as a component in composite materials, or mixed in contaminated waste streams, which require specific collection and sorting operations. The price of virgin material, which is highly volatile (between 0.5 and 0.8 EUR/kg), has a large influence on the profitability of recycling. In addition, the prices for landfilling and incineration are low. Nevertheless, in the coming years, it can be expected that the economic conditions for recycling are likely to improve, in particular due to the increasing costs for landfilling and incineration.
Future developments and policy orientations
In the baseline scenario about 9% of the total PVC waste could be mechanically recycled in 2010 and 2020, representing about 400,000 tonnes of PVC waste in 2010 and 550,000 tonnes in 2020 [50]. The recycling rates vary according to the specific waste streams considered.
[50] Prognos, op. cit.
* For high quality recycling, the following recycling rates could be reached for construction and demolition PVC wastes: about 25% for pipes, about 40% for window profiles and about 12% for flooring.
* For low-quality recycling, the recycling rates would be about 65% for cables present in the construction and demolition waste stream, about 30% for waste from electronic and electronic equipment and about 20% for packaging.
* Other waste streams such as household and commercial wastes are not likely to be recycled according to the assumptions made in this scenario.
Compared to this baseline scenario, maximum recycling potentials have been estimated [51], which represent the PVC quantities, which can be recycled, taking into account the technical and economic limits of PVC recycling. According to this scenario, the potential for post-consumer waste is about 800,000 tonnes in 2010 and 1.2 millions tonnes in 2020, representing a recycling rate of about 18%. This means that the mechanical recycling of PVC waste could contribute only to the management of about one fifth of PVC post-consumer waste. Other waste management routes will therefore remain important.
[51] Prognos, op. cit.
In its commitment of March 2000, the PVC industry has made quantified commitments regarding the mechanical recycling of pipes, fittings and window frames. For pipes, the commitment is "to recycle at least 50% of the collected available quantity of pipes and fitting waste by 2005". For window profiles, the commitment is "to recycle at least 50% of the collectable available quantity of window profiles waste by 2005". These targets are not based on waste generated but on waste collected.
According to the PVC industry, in 2005 the annually recycled quantities are estimated as follows: 15,000 tonnes for pipes and 15,000 tonnes for window profiles. However, the following large PVC waste streams, which could be used for high quality recycling, are not covered by the commitment: rigid profiles other than window profiles (about 240,000 tonnes in 2005), flooring calandered (about 240,000 tonnes in 2005) and flexible profiles and hoses (about 120,000 tonnes in 2005). Nonetheless, in its commitment, the PVC industry has stated that in the case of other potential applications such as PVC cables, flooring and roofing membranes, "more work is needed in developing suitable logistics, technologies and reuse applications". In addition, the industry has committed itself to supporting these developments including the achievement of higher mechanical recycling targets "as soon as possible."
Issues for consideration:
The Commission considers, on the basis of the above-mentioned analysis and given the present low recycling rate, that recycling of PVC should be increased. This could be done through a range of measures, which could be used separately or in combination. Their potential environmental and economic implications should be assessed. These potential measures include:
1. Mandatory collection and recycling targets for some relevant PVC waste streams
2. Voluntary commitment of the industry to improve and finance, totally or partially, the collection and the recycling of some relevant PVC waste streams
3. Recommendations to Member States with the objective of establishing and developing separate collection of PVC waste and other demolition waste
4. Development of appropriate standards that allow the use of recycled PVC materials
5. Marking of plastic products as a useful tool to facilitate the separation of PVC waste from the general waste stream and development of other methods for plastic identification and sorting
6. Development of innovative recycling processes for certain post-consumer PVC waste.
Question n°3: Which set of measures would be the most effective to reach the objective of an increase of PVC recycling-
The recycling of PVC waste containing heavy metals raises specific issues due to the potential dilution of heavy metals into new and possibly wider range of products. Some potential measures could be envisaged to address these issues. These measures should be assessed in the light of their potential environmental and economic implications. They include:
1. Legislative instruments to restrict the mechanical recycling of PVC waste containing lead and cadmium
2. Specific conditions for this recycling, such as recycling in the same type of application, the control of the placing on the market of recyclates, the marking of the recycled products and the control of the use of heavy metals
3. No specific conditions for this recycling.
Question n°4: Should specific measures be attached to the mechanical recycling of PVC waste containing lead and cadmium- If so, which ones-
4.3. Chemical recycling
Chemical recycling denotes a number of processes, by which the polymer molecules that constitute plastic materials are broken up into smaller molecules. These can either be monomers that can be used directly to produce new polymers or other substances that can be used elsewhere as starting materials in processes of the basic chemical industry.
In the case of PVC, in addition to the breaking up of the backbone of the polymer molecules, the chlorine attached to the chains is set free in the form of hydrogen chloride (HCl). Depending on process technology, HCl can be re-used after purification or has to be neutralised to form various products that either can be used or have to be disposed of.
In practice, during the last 5 years, there have been only a limited number of initiatives that have resulted in the construction of industrial plants, or may lead to the realisation of such plants in the near future. Chemical recycling processes can be categorised according to their capacity to handle waste with high or low chlorine content, 4 to 5% being the maximum PVC content that can be handled by technologies for low chlorine content. Of the three operational purpose-built chemical recycling plants for waste with low chlorine content, two have been shut down due to economic and supply reasons. For PVC-rich waste there is currently one incineration-based technology with HCl recovery operational, two pilots will become operational in the coming years.
According to several life cycle assessments (LCA), some chemical recycling processes would score considerably better with regards to energy use and global warming than municipal solid waste incineration and landfilling. In addition, in some processes chlorine is recovered, thus avoiding new production through energy-intensive chloralkali-electrolysis. The available LCAs did not allow a clear preference to be made for one of the chemical recycling technologies analysed. Direct mechanical recycling of PVC-rich waste is preferable in environmental terms, particularly if it concerns recycling to high-quality products, and does not involve extensive sorting and pre-treatment [52]
[52] TNO, Chemical recycling of plastics waste (PVC and other resins), Study for DG III, December 1999
Together with the organic parts in PVC, plasticisers are transformed into feedstock material as well. Stabilisers containing heavy metals mostly end up in solid residues that will most probably have to be landfilled. For most of the dedicated chemical recycling technologies, emissions of problematic substances other than solid residues are low [53]. No firm conclusions can be drawn with regard to the formation of dioxins. As a general rule, reducing conditions and high temperatures promote the breakdown and prevent the formation of dioxines, which is the case in some processes where the operating conditions avoid the formation of dioxins.
[53] TNO, op.cit.
It seems that chemical recycling of PVC-rich waste is unattractive in economic terms in those situations where mechanical recycling has proven already to be technically feasible, with the possible exception of flooring. This would imply that chemical recycling plants for PVC-rich waste would have to concentrate on those flows for which mechanical recycling is not feasible, e.g. for types of waste that cannot be mechanically recycled as they would require additional separation steps, contain too many problematic impurities, or because of other restrictions linked to environmental concerns.
Chemical recycling has to compete with other waste management practices in the EU, mainly based on landfill and incineration. Landfill and incineration have the lowest gate fees. Purpose-built chemical recycling plants will also face an important competition from blast furnace operations and cement kilns, which could absorb a large quantity of mixed plastics waste with limited PVC content.
When looking at the various waste streams, it appears that in the current situation for categories like agricultural waste, industrial waste and non-packaging household waste, chemical recycling, although technically feasible, will have problems to compete in the absence of legal or other steering instruments. As for automotive and electrical and electronic waste, the PVC content in the mixed plastics waste seem to be too high to make them suitable for most chemical recycling options for mixed plastics waste with low chlorine content, but too low for economically viable separation and subsequent treatment in plants for PVC-rich waste.
Overall, it can be concluded that the successful operation of dedicated chemical recycling plants is mainly dependent on the economic aspects and in present circumstances there are important question marks over the viability of such operations.
Future developments and policy orientations
Chemical recycling has a potential mostly for those wastes for which mechanical recycling is not an option, and when legal or other instruments are effective in steering the waste away from the most cost-effective competitors (such as cement kilns, municipal solid waste incinerators and landfill).
For 2010, the total PVC waste quantities, which could be chemically recycled in the baseline scenario, are about 80,000 tonnes as a fraction in mixed plastics waste with low chlorine content (mostly from packaging) and about 160.000 tonnes in mixed plastics fractions with higher PVC content, mostly from automotive and electric and electronic waste.
Industry committed to invest 3 million EUR by 2001 in a pilot plant, with the objective to recover the chlorine and hydrocarbons content of PVC coated fabrics. The outcome of this pilot will be known by mid 2002, when the decision to build a commercial plant will be made.
Issues for consideration:
The Commission notes with interest the efforts described above to develop further chemical recycling technologies. In this context, potential measures could be envisaged in order to encourage these developments. Their potential environmental and economic implications should be assessed. Such measures include:
1. Further voluntary initiatives from the PVC industry
2. Recommendations for targets for chemical recycling for those waste streams where mechanical recycling is not possible
3. Setting of mandatory targets for chemical recycling.
Question n°5: Which set of measures would be most appropriate for chemical recycling of PVC waste-
4.4. Other recycling and recovery technologies including co-incineration
A newly developed dissolution-precipitation process is based on physical principles without destruction of the polymer molecules to feedstock compounds. The process was developed specifically for composite materials containing PVC and other components. PVC is separated from the components that make up the composite through selective dissolution, and then the entire PVC compound is regenerated through precipitation. PVC and the other components can then be re-used.
Currently, an experimental installation is operational and a pilot plant is planned to be operational in 2001. The technology works in a closed circuit system, where the solvent is recycled.
The process deals with selectively collected PVC products. The quality has to be about the same as for mechanical recycling, which means that the costs of making the material available are comparable. The developers of this process expect that the technology could deal with rather complicated formulations, such as tarpaulins, cables, pharmaceutical blister packs, floor coatings, car dashboards, and could compete financially with some of the other recycling options.
Mixed plastic waste is used by one German steel producer as a reducing agent in blast furnaces in the production of raw iron. Mixed plastic waste is also used in cement kilns as a substitute to coal, oil or gas for the generation of heat.
The evaluation of the environmental performance of the use of mixed plastic waste in blast furnaces and cement kilns is somewhat controversial. According to some life cycle analyses, blast furnaces and cement kilns score better with regards to energy used and global warming than municipal solid waste incineration. With regards to the potential contribution of PVC to the emissions of dioxins, it is rather difficult to draw firm conclusions and further research would be necessary.
Blast furnaces and cement kilns can treat mixed plastic waste without the need for high capital investment, thus offering low gate fees. The use of mixed plastic waste in cement kilns and blast furnaces represents serious competition for other waste management installations. On the other hand, the use of mixed plastic waste in cement kilns and blast furnaces is restricted by its content in chlorine, as chlorine can have negative effects on the quality of the produced cement or iron and the potential corrosion of the equipment due to the formation of HCl. A tolerance of some 2-3% or less is possible [54]. Theoretically, co-combustion in cement kilns of mixed plastic waste with low PVC content could, however, become important in the future.
[54] Or some 1-1.5% chlorine. Values may vary per installation, and legal demands may vary per country.
4.5. Incineration
PVC waste, if incinerated, is mainly treated in municipal waste incinerators. PVC waste is also present in hospital waste incinerators since PVC applications are used in hospitals. Approximately 600,000 tonnes of PVC are incinerated per year in the Community. PVC represents about 10% of the plastic fraction incinerated and about 0.7% of the total quantity of waste incinerated [55].
[55] Bertin Technologies, cit. op.
PVC waste contributes between 38% and 66% of the chlorine content in waste streams being incinerated. The other main sources of chlorine are putrescibles (about 17%) and paper (10%). On average it can be estimated that about 50% of the chlorine input into the incinerators are due to the presence of PVC.
Upon incineration, PVC waste generates hydrochloric acid (HCl) in the flue gas, which needs to be neutralised except when a special technology is employed where HCl is reused. At the moment, this specific technology is used only in 5 plants in Germany and 3 plants are in construction. All acid gases generated during the incineration of municipal solid waste (in addition to HCl mainly sulphur oxides) have to be neutralised prior to emission of the remaining gas to the atmosphere. Community legislation [56] already requires emission limit values for hydrochloric acid. These limits are currently being revised into more stringent limits [57].
[56] Directive 89/369/EEC on the prevention of air pollution from new municipal waste incineration plants requires emission limit values for hydrochloric acid between 50 and 250 mg/Nm3 depending on the capacity of the incineration plant.
[57] The Proposal for a Directive on the incineration of waste [COM(1998) 558 final] as well as the Common Position on this Proposal [98/289 COD of 25 November 1999] foresees a strict emission limit value for HCl of 10 mg/Nm3, which will become in 2005 the emission limit value for existing and new incinerators in the Community.
In order to reach these emission limit values for HCl, neutralisation agents, in particular lime, are injected in order to neutralise the acidic components of the flue gas. The four main neutralisation processes are the dry, semi-dry, semi-wet wet and wet processes, which are presented in more details in annex 1.
An assessment [58] of the quantities of flue gas cleaning residues resulting from the incineration of PVC waste concluded that the incineration of 1kg of PVC generates on average [59] between 1 and 1.4 kg of residues for the dry process with lime, semi-dry and semi-wet wet processes. With the use of sodium hydrogen-carbonate as neutralisation agents in semi-dry process, 1 kg of PVC generates about 0.8 kg of residues. In case of wet processes, between 0.4 and 0.9 kg of liquid effluent is generated. There is an important difference between the amounts of neutralisation agent required and residues produced between soft and rigid PVC. Flexible PVC contains less chlorine than rigid PVC. The amounts of neutralisation agents required and of residues generated are therefore lower for flexible PVC than for rigid PVC (1 kg of soft PVC [60] generates between 0.5 and 0.78 kg of residues). More details can be found in the following table.
[58] Bertin Technologies, cit. op.
[59] The average figure apply to a PVC material mix with 45% chlorine, i.e. composed of 70% rigid PVC (containing 53% chlorine) and 30% flexible PVC (containing 25% chlorine)
[60] For these calculations, soft PVC contain 0.25% of chlorine
Table 3: Estimated quantities of residues generated by the incineration of 1 kg of PVC waste [61]
[61] Bertin Technologies, The influence of PVC on quantity and hazardousness of flue gas residues from incineration, Study for DG XI, April 2000
>TABLE POSITION>
The flue gas cleaning residues are classified as hazardous waste [62]. The residues are generated separately (in particular in semi-wet and wet systems) or mixed with fly ash. The residues contain the neutralisation salts, the excess neutralisation agent as well as pollutants such as heavy metals and dioxins that were not destructed. Landfilling of the residues is, with some exceptions, the only option used within the Member States.
[62] According to Council Decision 94/904/EC establishing a list of hazardous waste, OJ L 356 , 31/12/1994 p.14-22, all solid waste from gas treatment are classified as hazardous (code 190107).
Several processes have been devised to recover calcium chloride and sodium chloride from the residues of the dry and semidry processes, but few of them are currently used commercially. Except in some specific cases, it is uncertain whether such technologies can be commonly used in order to recover a substantial quantity of residues. These technologies would be "end of the pipe" solutions, less preferable than a preventive measure aimed at reducing at source the quantity of residues generated.
PVC at current levels in the municipal solid waste stream has the following effects on the flue gas cleaning residues in comparison to incineration of municipal solid waste without PVC [63]:
[63] Bertin Technologies, op. cit. The scenario considered is based on the incineration of 1 million tonnes of waste with and without PVC, respectively, and the landfilling of the resulting residues.
* PVC incineration contributes to an increase of the quantity of flue gas cleaning residues (about 37% for the dry systems, 34% for semi dry systems and 42% for semi wet-wet [64]).
[64] Bertin Technologies, op. cit.
* PVC incineration contributes to an increase of the content of leachable salts in the residues by a factor of two. These are primarily chlorides of calcium, sodium, and potassium.
* The incineration of PVC increases the amount of leachates from the residues put into landfill (about 19% for dry systems, 18% for semi dry systems, 15% for the semi wet-wet systems and 4% for wet systems). The leachates need to be treated prior to any discharge.
* There is a theoretical possibility that the leaching of, for example cadmium, may increase due to increased chloride complexation caused by PVC incineration but data would be needed to substantiate this.
* In the current temperature range of combustion steps for municipal solid waste incineration, the higher chlorine content has no significant effects on the transfer of heavy metals and trace elements from bottom ash to gas treatment residues.
The potential influence of the incineration of PVC waste on the emissions of dioxins has been at the centre of a major scientific debate since PVC is currently the largest contributor of chlorine into incinerators. The contribution of incinerators to the total emissions of dioxins in the Community was about 40% between 1993 and 1995 [65].
[65] Identification of relevant industrial sources of dioxins and furans in Europe, Landseumweltamt Nordrhein-Westfalen, Essen, 1997
It has been suggested that the reduction of the chlorine content in the waste can contribute to the reduction of dioxin formation, even though the actual mechanism is not fully understood. The influence on the reduction is also expected to be a second or third order relationship [66]. It is most likely that the main incineration parameters, such as the temperature and the oxygen concentration, have a major influence on the dioxin formation.
[66] Danish Environmental Protection Agency, Environmental aspects of PVC, 1996
Whilst at the current levels of chlorine in municipal waste, there does not seem to be a direct quantitative relationship between chlorine content and dioxin formation, it is possible that an increase of chlorine content in the waste stream above a certain threshold could contribute to an increase of the dioxin formation in incinerators. The threshold of 1% of chlorine has been suggested [67] but uncertainties remain on the level of this threshold [68]. Further assessment should be carried out in order to assess the threshold above which the chlorine content would influence the formation of dioxins. This threshold could be exceeded due to increasing quantities of waste containing chlorine.
[67] Wikstrom, 1996, influence of level and form of chlorine on the formation of chlorinated dioxins, dibenzofurans and benzenes during the combustion of an artificial fuel inn a laboratory reactor.
[68] Danish Environmental Protection Agency, Dioxins emissions from waste incineration, Environmental Project 117, 1989 Danish Environmental Protection Agency, The effects of chlorine content on the formation of dioxin, Project 118, 1989 Danish Environmental Protection Agency, Dioxins - sources, levels and exposures in Denmark, Working report N°50/1997
At present, not all incinerators in the Community are already operating according to state-of-the-art air-emission standards for dioxins. The Proposal for a Directive on the incineration of waste [69] foresees an emission limit value of 0,1 ng/m³. This shall decrease the emissions of dioxins from incinerators.
[69] [COM(1998) 558 final]
The potential link between the incineration of PVC and the corrosion of the equipment of incinerators has also been debated. Some operators claim that the steam pressure and consequently the energy efficiency could be higher with a lower chlorine presence in the waste stream. The absence of PVC could therefore enable a higher efficiency of the energy recovery system. This question needs further research. It should be noted that the incineration with energy recovery of PVC waste generates higher energy than the incineration of general municipal solid waste since the calorific value of PVC waste is higher [70].
[70] The average caloric value for flexible PVC is about 16 GJ/tonne, about 20 GJ/tonne for rigid PVC and about 10 GJ/tonne for municipal solid waste.
PVC waste incineration increases the operating costs of the incinerators due to the use of neutralisation agents to neutralise the acid flue gas and the additional costs for the waste management of the resulting residues. The total additional financial costs related to the incineration of PVC vary depending on the Member State, the neutralisation processes and the waste management of the residues. It is estimated that the additional costs of incinerating PVC compared to municipal solid waste is from about 20 EUR per tonne for wet systems to more than 300 EUR per tonne for dry systems [71]. Differences depend upon the technology used and the type of PVC incinerated (flexible or rigid). More details on these costs can be found in annex 2. These additional costs are at present not borne specifically by new PVC products or by PVC waste, but are included in the overall incineration cost of waste.
[71] Bertin Technologies, op. cit.
A study [72] has been commissioned to assess the economic implications of diverting PVC waste away from incineration. The report analyses three scenarios in comparison to the baseline scenario (see annex 3 for details). In the first and the second scenarios, recycling rates increase to 15% and 22% respectively in 2020, with a proportionate decrease in the amount of PVC sent to incineration and landfill. With regard to incineration this means a cumulative diversion of about 1,700 ktonnes for scenario 1 (mainly construction waste) and 3,800 ktonnes for scenario 2 in the time period 2000 to 2020. In the third scenario recycling rates are unchanged against the baseline scenario, but the incineration rate is estimated as 28% in 2020 instead of 45% as forecasted in the baseline scenario as a result of the diversion of construction waste to landfill. This corresponds to the diversion of about 10,300 ktonnes in the time period 2000 to 2020.
[72] AEA Technology, Economic evaluation of PVC waste management, a report produced for the European Commission Environment Directorate-General, June 2000. The study encompasses EU Member States + 6 Candidate countries. The reported figures relate to the average between the "high" and the "low" incineration scenarios. These scenarios are based on the assumption that landfilling of PVC waste would be significantly reduced in some countries such as Sweden, Austria, Germany and the Netherlands. The difference relates to the degree of reduction achieved. Values shown refer to a 4% discount rate.
The financial costs considered for scenarios 1 and 2 include the avoided cost of incineration (including "specific costs" [73]) and the incurred net cost of the recycling process which depends on the waste stream diverted. The specific costs of incineration vary considerably depending upon the types of flue gas cleaning systems. Calculations in the report have been carried out for an "average" system distribution consisting of 25% semi dry-systems, 25% wet systems and 50% semi-wet wet systems. The results show that except in the case of rigid construction products (pipes, windows, cable trays and other rigid profiles) and cables, diversion of PVC waste from incineration to recycling results in a net increase in costs. The costs per tonne diverted have been estimated to be about 50 EUR/tonne for scenario 1 and about 190 EUR/tonne for scenario 2. Scenario 3 results in a net saving of about 90 EUR/tonne. These latter savings are mainly due to the lower cost of landfill and to the assumption that segregation of construction waste is generally carried out on site at the expense of the waste generator. Diversion of other waste streams to landfill (e.g. household and commercial waste) would result in much higher costs.
[73] Incineration of PVC with municipal solid waste (MSW) incurs additional operating costs for the incinerator in terms of reagents to abate acid gas emissions and for the treatement and disposal of residues, although these are partly offset by increased energy sales due to the higher calorific value of PVC compared to MSW.
The main environmental burdens including the related human health impacts of the three scenarios have been assessed. To the extent possible, and therefore with a bias towards impacts of air pollution, the external costs associated to each scenario have been evaluated. The calculations for all the scenarios show environmental benefits. Considering what is regarded in the study as being the "best" estimate for each of the burdens evaluated, benefits have been estimated for the three scenarios to be respectively about 190, 140 and 50 EUR per tonne of waste diverted for the period 2000-2020. The major contribution to these results comes firstly from the avoided emissions from the manufacture of virgin PVC (in the case of high quality recycling) and secondly from the avoided emissions from incineration (including indirect emissions associated with the manufacture of neutralisation agents).
It can be seen from the comparison between the financial and the environmental analyses based on the best estimate that scenario 1 and scenario 3 show an overall benefit, as the costs per tonne diverted are lower than the benefits. The contrary is true for scenario 2, where the environmental benefit (although higher than in scenario 1 and 3) is nevertheless exceeded by the estimated cost.
A number of assumptions have been made to carry out these calculations. In particular, concerning the financial aspects, the cost elements were necessarily based on very few experiences of existing PVC post-consumer waste recycling schemes, which are still at a preliminary stage. These uncertainties are higher for scenario 2. As the price of recyclates is closely linked to the price of virgin PVC, increasing prices of the latter would lead to lower overall costs.
As indicated, the environmental analysis is biased towards the impacts of air pollution. However, it is likely that most of the externalities omitted (e.g. residues disposal) would increase the benefits of the diversion of PVC from incineration. The main exception relates to phthalate plasticisers. Landfilled flexible PVC would form a reservoir of these chemicals that could slowly leach out over time, whilst incineration presents the advantage of destroying them. Incineration also allows the recovery of the calorific value of phthalates. This factor has been included in the environmental analysis.
Future developments and policy orientations
In the baseline scenario, the incineration of PVC waste would increase to about 2.5 millions tonnes in 2020 compared to about 600,000 tonnes at present. The number and capacity of incinerators employing wet, semi-wet wet and semi-dry flue gas neutralisation technologies will increase at the expense of those employing dry technologies.
Issues for consideration:
The Commission considers, on the basis of the above-mentioned analysis, that the incineration of PVC waste raises a number of issues. A range of measures could be envisaged to address these issues and should be assessed in the light of their potential environmental and economic implications. Such measures include:
1. Diversion of PVC waste, mandatory or not, as far as economically feasible, from incineration to preferably recycling or landfilling. This would require the introduction of collection schemes to ensure separate collection of PVC to be diverted
2. Similar diversion only for rigid PVC
3. Meeting the additional costs related to the incineration of (totally or partially), e.g. through internalisation of these costs in the price of new PVC products or direct financial contribution to operators of incineration plants
4. Encouragement of the conversion of the flue gas cleaning technologies that reduce the amounts of residues generated or allow the recycling of HCl instead of its neutralisation
5. Further research on the potential relation between PVC incineration and dioxin formation should be carried out.
Question n°6: Which set of measures would be most effective to address the issues linked to the incineration of PVC waste-
4.6. Landfill
Landfilling is the most common waste management route for PVC waste. Exact figures on the landfilling of PVC waste are not known and there are large differences between various estimations ranging up to 2.9 million tonnes of PVC waste being landfilled every year. It can be estimated that several tens of million tonnes of PVC waste have already been landfilled during the past 30 years.
Member States will have to bring into force the provisions of Directive 1999/31/EC on the landfilling of waste in 2001. The Directive requires that landfill installations comply with a number of technical standards regarding the protection of soil and water including leachate collection, bottom sealing and gas emission control.
All materials in landfill including PVC are subject to different reactive conditions, which are determined by the parameters such as temperature, moisture, presence of oxygen, activity of micro-organisms and the interactions between parameters at different stages of the ageing process of landfills. Four main phases can be distinguished: short initial aerobic phase, anaerobic acidogenic phase (variable duration, longer than aerobic phase), anaerobic methanogenic phase (up to several centuries), final aerobic phase.
Investigations [74] have been carried out on both rigid and soft PVC samples mainly through laboratory equipment studies, examination of the effects of a biological treatment, and of microbiogical tests.
[74] Argus in association with University Rotstock, op. cit.
The PVC polymer is generally regarded as being resistant under soil-buried and landfill conditions [75]. However, an attack on the PVC polymer of a thin packaging foil has been detected [76]. This remains an isolated result and the attack was observed under aerobic conditions and at 80°C, conditions which, if they occur in landfills, are transient.
[75] Mersiowski et al. 1999, Behaviour of PVC in landfills, ECVM, Technical University Hamburg-Harburg
[76] Argus in association with University Rotstock, op. cit.
Losses of plasticisers, especially phthalates, from flexible PVC are widely recognised in the literature. Results from studies on the degradability of phthalates under landfill conditions show that degradation of phthalates occurs, but may not be complete depending on conditions and type of phthalate. Both, phthalates and their degradation substances can be detected in landfill leachates. In addition, long-chain phthalates, such as DEHPs, are only partly degraded in usual leachate and sewage treatment plants and accumulate on suspended solids. Losses of phthalates could also contribute to gaseous emissions from landfills. As for other emissions from landfill, emissions resulting from the presence of PVC in landfills can last longer than the guarantee of the technical barrier and there is no evidence that the release of phthalates will come to a standstill after a given period of time.
Stabilisers are encapsulated in the matrix of rigid PVC waste. Hence, migration is expected to be low and would affect the surface of the PVC but not the bulk of the material. Concerning stabilisers in flexible PVC waste, a study [77] into the long-term behaviour of PVC waste under landfill condition showed a release of lead stabiliser from one specific PVC cable containing a combination of several plasticisers.
[77] Mersiowski et al., op. cit.
PVC products disposed of in landfills will certainly contribute to the formation of dioxins and furans during accidental landfill fires, but the quantitative contribution cannot currently be estimated due to the inherent difficulties in obtaining the necessary data.
In order to further assess and quantify the environmental impacts of the landfilling of PVC, further research would be necessary to study the potential degradation of PVC polymer, the release of stabilisers and plasticisers, as well as the environmental contribution of phthalates to the leachates and gaseous emissions from landfills.
The costs for landfilling PVC waste in Member States are those for landfilling municipal solid waste and show a wide range of tariffs [78]. The prices or tariffs for landfills are influenced by a number of factors such as the standard of the landfill, the competition between different disposal routes, the type and nature of waste being accepted. Generally, no influence on prices or tariffs could be related or is expected due to the presence of PVC in municipal solid waste being landfilled.
[78] At present, the costs for landfilling municipal solid waste range from 8 EUR per tonne in Spain up to 200 EUR per tonne in Germany. The cost for landfilling mixed waste, such as unsorted construction and demolition waste containing organic components, is usually higher than for landfilling of inert waste. An average price of about 50 EUR per tonne is usual.
Future developments and policy orientations
In the baseline scenario, it is expected that the quantities of PVC waste landfilled would remain constant at about 2.8 millions tonnes in 2020.
Issues for consideration:
The Commission considers, on the basis of the previous analysis, that the landfilling of flexible PVC waste raises some issues. A range of measures could be envisaged to address these issues. Environmental and economic implications of these measures should be considered. Such measures include:
1. Disposal of flexible PVC waste in controlled landfill sites with high emission standards as foreseen in the landfill Directive
2. Further research on the leaching or emissions of additives.
Question n°7: Are specific measures concerning the landfilling of PVC waste necessary- If so, which ones-
5. Other horizontal aspects on PVC
The analysis in this document focuses on two main aspects : the use of additives in PVC and the management of PVC waste. In addition, more general and horizontal aspects arise in the context of a broad consultation on PVC.
Regarding the type of instruments to implement a horizontal Community strategy on PVC, a range of measures, mandatory and voluntary, is available:
* Voluntary approaches, including the implementation of existing voluntary commitments, at national and Community levels, as well as the development of new voluntary approaches. As mentioned previously, the European PVC industry has signed a voluntary commitment on the sustainable development of PVC. And while this can be seen as a first step there is still work to be done to ensure an effective participation by industry in achieving Community goals in this area. It should be underlined that the services of the Commission are currently preparing a Proposal for a framework Regulation concerning Community environmental agreements to be adopted by Council and Parliament.
* Legislative measures, such as a Proposal for a Directive on PVC, could be proposed in order to address issues related to management of PVC waste and other legislative measures to deal with the use of additives on the basis of all existing scientific evaluation, including the results of risk assessments. Recommendations could also be adopted to develop the implementation of a Community strategy.
* A mix of instruments could be proposed, integrating voluntary commitments, recommendations and regulations including the adaptation of existing legislation. Such a set of instruments would be in line with an approach, which aims at combining voluntary and binding instruments.
Apart from an approach based on PVC waste management and additives, the question of a potential substitution policy for certain PVC applications has been raised in the context of promoting more sustainable products as part of an Integrated Product Policy. Such a substitution policy could be considered for specific applications, which can not be separated from the general waste stream and therefore are difficult to recycle such as in packaging, motor vehicles, electric and electronic equipment. A potential substitution policy would need to be underpinned by a comprehensive and objective assessment of the main environmental impacts both of PVC and of potential substitutes during their whole life cycle. The approach outlined in this document focuses on dealing with the environmental issues of PVC mainly through policies on additives and waste management.
Issues for consideration:
A number of issues regarding the environmental impacts of PVC have been identified, including the question of a horizontal approach and of appropriate instruments to address these issues. The Commission sees merit in developing a horizontal strategy on PVC. A number of instruments are available to implement such an approach. Environmental and economic implications, as well as the compatibility with the international obligations of the Community should be assessed.
Question 8: Which are the appropriate instruments for developing a horizontal strategy on PVC- Should a PVC substitution policy for some specific applications be envisaged- If so, how-
6. Conclusion
A number of concerns regarding the impact of PVC on the environment, including related human health issues, have been identified and explained in this document. These are mostly related to the use of certain additives and to the management of PVC waste. In the light of the analysis, a number of options have been identified, which could ensure an effective approach on waste management and additives, to be based on an assessment of the environmental and economic implications, with a view to reducing the impact on human health and the environment of PVC throughout its life cycle.
A public consultation on PVC is proposed on the basis of these options. The Commission hereby invites all interested parties to discuss and comment on this document. A public hearing will be organised in October 2000.
Comments may be sent directly to the Commission at the latest on 30 November 2000. Submissions should be sent to Mr Krämer, Head of the waste management unit (DG ENV) and Mr Schulte Braucks, Head of the chemicals unit (DG ENTR), 200 rue de la Loi / Wetstraat 200, B-1049 Bruxelles/Brussel, Belgium. Comments may alternatively be sent by e-mail to the following address: ENV-PVC@cec.eu.int. The various language versions of the Green Paper, the studies commissioned by the Commission as well as the comments on the Green Paper can be found at the following internet address: http://europa.eu.int/comm/environment/pvc/index.htm.
On the basis of the analyses developed in this document and the outcome of this consultation process, the Commission will present at the beginning of 2001 a Communication setting out a comprehensive Community strategy on the environmental issues of PVC.
ANNEX 1
Description of the various flue gas cleaning processes
Flue gas cleaning processes // Main characteristics
Dry process // The neutralisation process consists of the injection of solid neutralisation agents. The most common neutralisation agent is lime (Ca(OH)2). Other agents are also used, in particular sodium hydrogen-carbonate (Bicar, NaHCO3) or spongiacal hydrated lime.
A chemical reaction transforms the acidic components of the flue gas into salts. The resulting residues of the neutralisation process are solid residues mainly composed of neutralisation salt: calcium chloride (CaCl2), sodium chloride (NaCl), sulphates (CaSO4, Na2SO4), excess of the neutralisation agents and heavy metals in various chemical forms. These residues are classified as hazardous waste.
The dry process with classical lime is not likely to be able to comply with the strict emission limit value of 10 mg/Nm3. The dry processes using specific neutralisation agents such as spongiacal hydrated lime and Bicar can comply with this limit.
Semi-dry process // The neutralisation process consists of the injection of a solution or a suspension of the neutralisation agent (lime) in water. The resulting reaction products are solid residues. They are composed of calcium chloride, sulphates and heavy metals, as well as unreacted lime added in excess. The residues are classified as hazardous waste.
Wet process // In this process, two successive scrubbers are operating. In the first (acid scrubber), most of the HCl is absorbed in water. The remaining HCl and SOx are absorbed and neutralised in the second scrubber (neutral scrubber), which is generally fed with a soda (NaOH) solution.
The resulting liquid effluents need to be treated prior to release into the environment. In the water treatment unit, heavy metals and sulphates are precipitated by the addition of lime. The precipitated heavy metals are separated by filtration (and need to be landfilled), while the treated saline wastewater is discharged.The effluent of the acidic scrubber is either neutralised and treated together with the effluent of the neutral scrubber or is purified and HCl reused.
Semi-wet wet process // Due to stricter regulations on the discharge of saline wastewater, many incineration plants are introducing evaporation to eliminate liquid discharges completely [79]. Wet processes are therefore being converted to semi wet-wet processes generating dry solid residues. This is already the case for German and Austrian plants. This process is similar to the wet technique but the liquid effluent is then sprayed in the gas and the liquid evaporated. This system produces dry residues classified as hazardous waste.
[79] Economic evaluation of the Draft Incineration Directive, a report produced for the European Commission, DG XI, AEA Technology, December 1996
It is difficult to present a detailed repartition of the various types of incinerators currently in activity. The following statistics [80] present the situation for the period 1993-1996 and for plants with a rather large capacity. About 15% of the total capacity use a dry process for gas treatment, for 25% a semi-dry process is employed, for about 20% semi-wet wet processes are in use and about 40% wet processes are used. The distribution of treatment capacities is different in the various Member States. In general, the capacities for dry processes have decreased at the expense of other processes. The stricter emission requirements for incinerators as proposed in the Directive on waste incineration are likely to enhance this trend.
[80] European Energy from Waste Coalition, Energy from Waste Plants: Databook of European Sites, Report prepared by Juniper Consultancy Services Ltd, November 1997. This figure refers to plants with a capacity of more than 30,000 t/year.
ANNEX 2
Additional cost for PVC incineration
The figures in the following table [81] represent the range of additional costs for the incineration of PVC in comparison to municipal solid waste. The lower figures apply to flexible PVC containing 25% chlorine, the higher figures to rigid PVC containing 53% chlorine. The average figures apply to a PVC material mix with 45% chlorine, i.e. composed of 70% rigid PVC and 30% flexible PVC.
[81] Bertin Technologies, The influence of PVC on quantity and hazardousness of flue gas residues from incineration, Study for DG XI, April 2000
>TABLE POSITION>
ANNEX 3
PVC waste management scenarios established for the economic and environmental analysis [82]
[82] AEA Technology, Economic evaluation of PVC waste management, draft report produced for the European Commission Environment Directorate-General, May 2000
Scenarios of future waste management across the EU and six of the applicant countries have been developed in order to carry out the economic and environmental analysis. The business as usual (BAU) scenario is based on current destination of PVC waste across Western Europe as made available by EuPC and the present rate of MSW incineration. The present day incineration rate of main PVC waste streams is assumed to be in proportion to the general rate for MSW incineration. To estimate future destinations, a distinction has been made between Member States which will limit themselves to the strict implementation of the landfill directive and Member States which are likely to go beyond EU rules, substantially reducing the landfilling of raw organic waste (e.g. Austria, Germany, the Netherlands, Sweden) by increasing incineration. The first group of Member States are also expected to increase incineration capacity over the next two decades, but the final rate achieved is assumed to be lower because of the lower starting point and the poorer economic circumstances of some of the countries concerned. Accession countries have been included in this first group.
The obtained incineration rates have been applied to the remaining quantities after deduction of PVC waste that is mechanically recycled. Given the current limited state of its development, feedstock recycling has not been considered in the study. Mechanical recycling has been assumed to develop as predicted under the baseline scenario developed in the mechanical recycling study [83]. Thus recycling of post-consumer PVC waste will increase from about 3 per cent today to about 9 per cent by 2020.
[83] Prognos, op.cit.
Three alternative scenarios for diversion of PVC from incineration have then been elaborated. The first two are based on the assumption that PVC diverted from incineration will go to mechanical recycling. In the third scenario, diverted waste is sent to landfill.
Scenario 1: This scenario is partly based on the "selective improvement scenario" proposed in the mechanical recycling study. It is assumed that recycling of most construction wastes suitable for high quality recycling is encouraged so that the average potential calculated in the mechanical recycling study is reached. Although suitable for high quality recycling, PVC in the household and commercial waste category as well as flexible profiles and hoses (construction category) have however been excluded as no precise cost estimate was available. It is reasonable to assume that development of recycling potential for these wastes is therefore further away than for the remaining wastes for which cost estimates were provided.
Scenario 2: This scenario models mechanical recycling for all suitable types of waste (construction, household and commercial, packaging, electric and electronic waste) achieving its absolute full potential in 2010 and continues at this rate until 2020. All waste streams are recycled at the maximum of recycling potential estimated in the mechanical recycling study.
Scenario 3: In this scenario recycling rates remain unchanged compared to the baseline scenario. PVC waste diverted from incineration is therefore sent to landfill. The analysis is limited to the diversion of construction waste to identify the main economic and environmental impacts of diverting from incineration to landfill. Segregation of PVC from the other waste streams considered in the study is likely to be more problematic from an economic and technical perspective.