Proposal for a Council Decision establishing criteria and procedures for the acceptance of waste at landfills pursuant to Article 16 and Annex II of Directive 1999/31/EC on the landfill of waste
Date: 2002-09-20
Institutions: European Commission
Subjects: data collection, environmental protection, environmental risk prevention, technical regulations, testing, underground storage of waste, waste management

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Proposal for a Council Decision establishing criteria and procedures for the acceptance of waste at
landfills pursuant to Article 16 and Annex II of Directive 1999/31/EC on the landfill of waste

(2003/C 20 E/16)

COM(2002) 512 final

(Submitted by the Commission on 20 September 2002)

EXPLANATORY MEMORANDUM

1. Directive 1999/31/EC on the landfill of waste distinguishes between three classes of landfills:

— landfills for hazardous waste

— landfills for non-hazardous waste

— landfills for inert waste

2. Pursuant to Article 6 of the Directive:

Only hazardous waste that fulfils the relevant criteria set out in Annex II may be assigned to landfills
for hazardous waste.

Landfills for non-hazardous waste may be used for municipal waste, for other non-hazardous waste that
fulfils the relevant criteria set out in Annex II and for stable, non-reactive hazardous waste that fulfils
the relevant criteria set out in Annex II.

Landfills for inert waste shall be used only for inert waste.

3. Annex II of the Directive lays down the principles for waste acceptance criteria and procedures, as well
as preliminary criteria and procedures to be applied before Community criteria and procedures are
established.

4. Pursuant to Article 16 of the Directive, the Commission shall set specific criteria and/or test methods
and associated limit values for each landfill class, including if necessary specific types of landfills within
each class, including underground storage. The Commission will be assisted by the Committee estab-
lished by Article 18 of Directive 75/442/EEC on waste. In this work the general principles and the
general procedures for testing and acceptance criteria set out in Annex II shall be taken into account.
The work shall be completed at the latest by 16 July 2002.

5. The Commission has drawn up a draft of the measures to be taken.

This draft decision lays down:

— the procedures for characterising waste, checking compliance of the waste with the acceptance
criteria and the on-site verification that the waste arriving at the landfill is identical to the waste
described in the documents,

— acceptance criteria for inert waste, for certain non-hazardous wastes (only those that are landfilled
together with stable, non reactive hazardous waste),
for stable non-reactive hazardous waste
accepted at landfills for non-hazardous waste, for hazardous waste and for underground storage,

— the test methods to be used.

6. The draft decision was submitted to vote in the Committee established under Article 18 of Directive
75/442/EEC on waste on 23 July 2002. There was no qualified majority in favour of the draft decision.

Thus, in accordance with the procedure set out in Article 18 of Directive 75/442/EEC a Proposal for a
Council Decision is submitted to Council. If Council has not acted within three months from the date of
referral of the proposal, the proposed measures shall be adopted by the Commission.

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THE COUNCIL OF THE EUROPEAN UNION,

HAS ADOPTED THIS DECISION:

Article 1

This Decision establishes the criteria and procedures for the
acceptance of waste at landfills in accordance with the prin-
ciples set out in Directive 1999/31/EC and in particular its
Annex II.

Article 2

Member States shall apply the procedure as set out in section 1
of the Annex to this Decision to determine the acceptability of
waste at landfills.

Article 3

Member States shall ensure that waste is only accepted at a
landfill, if it fulfils the acceptance criteria of the relevant landfill
class as set out in section 2 of the Annex to this Decision.

Article 4

The sampling and testing methods listed in section 3 of the
Annex to this Decision shall be used for determining the
acceptability of waste at landfills.

Article 5

Without prejudice to existing Community legislation,
the
in the Annex to this
criteria and procedures as set out
Decision will not apply to waste resulting from prospecting,
extraction,
treatment and storage of mineral resources and
from the working of quarries, when they are deposited
In the absence of specific Community legislation,
on-site.
Member States shall apply national criteria and procedures.

Article 6

1.

This Decision will enter into force on 16 July 2004.

2. Member States shall apply the criteria set out in section 2
of the Annex to this Decision at the latest by 16 July 2005.

Article 7

This Decision is addressed to the Member States.

Having regard to the Treaty establishing the European
Community,

Having regard to Directive 1999/31/EC on the landfill of
waste (1), and in particular Article 16 and Annex II thereof,

Whereas:

(1) Pursuant

to Article 16 of Directive 1999/31/EC the
Commission shall
test
methods and associated limit values for each class of
landfill.

specific

criteria

and/or

adopt

(2) A procedure should be laid down to determine the accepta-

bility of waste at landfills.

(3) Limit values and other criteria should be set for waste

acceptable at the different classes of landfills.

(4) The test methods to be used for determining the accepta-

bility of waste at landfills should be determined.

(5) It is appropriate from a technical point of view to exempt
from the criteria and procedures set out in the Annex to
this Decision those wastes generated by the extractive
industry that are deposited on-site.

(6) A suitably short transition period should be granted to
Member States to develop the necessary system to apply
this decision and a further brief transition period may be
necessary for Member States to ensure the application of
the limit values.

(7) The measures provided for in this Decision are not in
accordance with the opinion of the Committee established
by Article 18 of Directive 75/442/EEC on waste (2). They
must therefore be adopted by the Council in accordance
with Article 18, paragraph 4 of Directive 75/442/EEC,

(1) OJ L 182, 16.7.1999, p. 1.
(2) OJ L 78, 26.3.1991, p. 32.

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CRITERIA AND PROCEDURES FOR THE ACCEPTANCE OF WASTE AT LANDFILLS

ANNEX

INTRODUCTION

This annex lays down the uniform waste classification and acceptance procedure according to Annex II of Directive
1999/31/EC on the landfill of waste.

In accordance with Article 176 of the Treaty, Member States are not prevented from maintaining or introducing more
stringent protective measures than those established in this Annex, provided that such measures are compatible with the
Treaty. Such measures shall be notified to the Commission. This could be of particular relevance with reference to the
limit values for Cadmium and Mercury in Section 2.

Section 1 of this annex lays down the procedure to determine the acceptability of waste at landfills. This procedure
consists of the basic characterisation, compliance testing and on-site verification.

Section 2 of this annex lays down the acceptance criteria for each landfill class. Waste may only be accepted at a landfill
if it fulfils the acceptance criteria of the relevant landfill class as laid down in section 2 of this annex.

Section 3 of this annex lists the methods to be used for the sampling and testing of waste.

Annex A defines the safety assessment to be carried out for underground storage.

Annex B is an informative annex providing an overview of the landfill options available within the Directive and
examples of possible sub-categorisation of landfills non-hazardous waste.

1.

PROCEDURE FOR THE ACCEPTANCE OF WASTE AT LANDFILLS

1.1.

Basic characterisation

Basic characterisation is the first step in the acceptance procedure and constitutes a full characterisation of the
waste by gathering all the necessary information for a safe disposal of the waste in the long term. Basic
characterisation is required for each type of waste.

1.1.1.

The functions of basic characterisation are the following

(a) Basic information on the waste (type and origin, composition, consistency, leachability and other char-

acteristic properties).

(b) Basic information for understanding the behaviour of waste in landfills and options for treatment for Article

6 (a).

(c) Assessing waste against limit values.

(d) Detection of key variables (critical parameters) for compliance testing and options for simplification of
compliance testing (leading to a significant decrease of constituents to be measured, but only after demon-
stration of relevant information). Characterization may deliver ratios between basic characterisation and
results of simplified test procedures as well as frequency for compliance testing.

If the basic characterisation of a waste shows that the waste fulfils the criteria for a landfill class as laid down in
section 2 of this annex, the waste is deemed to be acceptable at this landfill class. If this is not the case, the
waste is not acceptable at this landfill class.

The producer of the waste, or in default the person responsible for its management, is responsible for ensuring
that the characterisation information is correct.

The operator shall keep records of the required information for a period that will be defined by the Member
State.

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1.1.2.

The basic requirements for basic characterisation of the waste are the following

(a) Source and origin of the waste

(b) Information on the process producing the waste (description and characteristics of raw materials and

products)

(c) Description of the waste treatment applied in compliance with Article 6(a), or a statement of reasons why

such treatment is not considered necessary

(d) Data on the composition of the waste and the leaching behaviour, where relevant (as a general rule the
mandatory parameters in section 2 have to be tested; testing of other parameters has to be decided on a
case by case basis)

(e) Appearance of the waste (smell, colour, physical form)

(f) Code according to the European Waste List (Decision 2001/118/EC)

(g) For hazardous waste in case of mirror entries: the relevant hazard properties according to Annex III of

Directive 91/689/EC

(h) Information to prove that

the waste does not fall under the exclusions of Article 5.3 of Directive

1999/31/EC

(i) The landfill class at which the waste may be accepted

(j) Additional precautions to be taken at the landfill

(k) Check if the waste can be recycled or recovered.

1.1.3.

Testing

As a general rule a waste must be tested to obtain the above information. In addition to the leaching behaviour,
the composition of the waste must be known or determined by testing. The tests used for basic characterisation
must always include those to be used for compliance testing.

The content of the characterisation, the extent of laboratory testing required and the relationship between basic
characterisation and compliance checking depends on the type of waste. A differentiation can be made
between:

(a) wastes that are regularly generated in the same process,

(b) wastes that are not regularly generated.

The characterisations outlined in (a) and (b) will provide information that can be directly compared with
acceptance criteria for the relevant class of landfill and, in addition, descriptive information can be supplied
(e.g. the consequences of depositing with municipal waste).

(a) Wastes regularly generated in the same process.

These are individual and consistent wastes regularly generated in the same process, where:

— the installation and the process generating the waste are well known and the input materials to the process

and the process itself are well defined;

— the operator of the installation provides all necessary information and informs the operator of the landfill

of changes to the process (especially changes to the input material).

The process will often be at a single installation. The waste can also be from different installations, if it can be
identified as single stream with common characteristics within known boundaries (e.g. bottom ash from the
incineration of municipal waste).

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For these wastes the basic characterisation will comprise the basic requirements of basic characterisation and
especially the following:

— compositional range for the individual wastes;

— range and variability of characteristic properties;

— if required, the leachability of the wastes determined by a batch leaching test and/or a percolation test

and/or a pH dependence test;

— key variables to be tested on a regular basis.

If the waste is produced in the same process in different installations, information must be given on the scope
of the evaluation, i.e. whether the whole waste stream is of concern or only part, and if so how is that part
characterised/identified.

For such wastes, sufficient measurements must be carried out to demonstrate consistency of the waste.

For wastes from the same process in the same installation, the results of the measurements may show only
slight variations of the properties of the waste at a level significant in comparison with the appropriate limit
values. The waste can then be considered characterised and further deliveries are subject to compliance
checking only, unless significant changes in the generation processes occur.

For wastes from the same process in different installations, a more detailed evaluation is necessary. This means
that more measurements are needed. The results of the measurements must show the range and variability of
the characteristic properties. The waste can then be considered characterised and further deliveries are subject
to compliance checking only, unless significant changes in the generation processes occur.

Waste from facilities for the bulking or mixing of waste, from waste transfer stations or mixed waste streams
from waste collectors, can vary considerably in their properties. This must be taken into consideration in the
basic characterisation. Such wastes may fall under case (b).

(b) Wastes that are not regularly generated.

These wastes are not regularly generated in the same process in the same installation and are not part of a
well-characterised waste stream. Each batch produced of such waste will need to be characterised. The basic
characterisation shall include the basic requirements for basic characterisation. As each batch produced has to
be characterised, no compliance testing is needed.

1.1.4.

Cases where testing is not required

Testing for basic characterisation can be dispensed with in the following cases:

(a) The waste is on a list of wastes not requiring testing as laid down in point 2 of this annex.

(b) All the necessary information, for the basic characterisation, is known and duly justified to the full satis-

faction of the competent authority.

(c) Certain waste types where testing is impractical or where appropriate testing procedures and acceptance
criteria are unavailable. This must be justified and documented, including the reasons why the waste is
deemed acceptable at this landfill class.

1.2.

Compliance testing

When a waste has been deemed acceptable for a landfill class on the basis of a basic characterisation pursuant
to section 1 of this document, following deliveries of the waste shall be subject to compliance testing to
determine if the waste complies with the results of the basic characterisation and the relevant acceptance
criteria as laid down in section 2.

The function of compliance testing is to periodically check regularly arising waste streams.

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The relevant parameters to be tested are determined in the basic characterisation. Parameters should be related
to basic characterisation information; only a check on critical parameters (key variables), as determined in the
basic characterisation, is necessary. The check has to show that the waste meets the limit values for the critical
parameters.

The tests used for compliance testing shall be one or more of those used in the basic characterisation. The
testing shall consist at least of a batch leaching test. For this purpose the methods listed under section 3 shall be
used.

Wastes that are exempted from the testing requirements for basic characterisation, are also exempted from
compliance testing. They will, however, need checking for compliance with level 1 information.

Compliance testing shall be carried out at least once a year and the operator must, anyway, ensure that
compliance testing is carried out in the scope and frequency determined by basic characterisation.

Records of the test results shall be kept for a period that will be determined by the Member State.

1.3.

On-site verification

Each load of waste delivered to a landfill shall be visually inspected before and after unloading. The required
documentation shall be checked.

For wastes deposited by the waste producer at a landfill in his control, this verification may be made at the
point of dispatch.

The waste may be accepted at the landfill, if it is the same as that which has been subjected to basic char-
acterisation and compliance testing and which is described in the accompanying documents. If this is not the
case, the waste must not be accepted.

Member States shall determine the testing requirements for on-site verification, including where appropriate
rapid test methods.

The samples taken shall be kept after acceptance of the waste for a period that will be determined by the
Member State.

2.

WASTE ACCEPTANCE CRITERIA

This section sets out the criteria for the acceptance of waste at each landfill class,
underground storage.

including criteria for

Higher limit values for specific parameters listed in this section are acceptable, if

— a risk assessment shows that there is no risk for the environment,

— the competent authority gives a permit in a cases by case decision for the landfill and

— the permitted limit values do not exceed the limit values set out in this section by more than three times.

Member States shall define criteria for compliance with the limit values set out in this section.

2.1.

Criteria for landfills for inert waste

2.1.1.

List of wastes acceptable at landfills for inert waste without testing

Wastes on the following short list are assumed to fulfil the criteria as set out in the definition of inert waste in
Article 2(e) and the criteria listed in 2.1.2. The wastes can be admitted without testing at a landfill for inert
waste.

The waste must be a single stream and single source material. Different wastes contained in the list may be
accepted together, provided they are from the same source.

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In case of suspicion of contamination (either from visual inspection or from knowledge of the origin of the
waste) testing should be applied or the waste refused. If the listed wastes are contaminated or contain other
material or substances such as metals, asbestos, plastics, chemicals, etc. to an extent which increases the risk
associated with the waste sufficiently to justify their disposal in other classes of landfills, they may not be
accepted in a landfill for inert waste.

If there is a doubt that the waste fulfils the definition of inert waste according to Article 2(e) and the criteria
listed in 2.1.2 or about the lack of contamination of the waste, testing must be applied. For this purpose the
methods listed under section 3 shall be used.

EWC Code

Description

Restrictions

10 11 03

15 01 07

17 01 01

17 01 02

17 01 03

17 01 07

17 02 02

17 05 04

19 12 05

20 01 02

20 02 02

Waste glass based fibrous materials

Only without organic binders

Glass packaging

Concrete

Bricks

Selected C&D waste only (1)

Selected C&D waste only (1)

Tiles and ceramics

Selected C&D waste only (1)

Mixtures of concrete, bricks,
ceramics

tiles and

Selected C&D waste only (1)

Glass

Soil and stones

Glass

Glass

Soil and stones

Excluding topsoil, peat; excluding soil and
stones from contaminated sites

Separately collected glass only

from garden and parks waste;

Only
Excluding top soil, peat

(1) Selected construction and demolition waste (C&D waste): with low contents of other types of materials (like metals, plastic,

soil, organics, wood, rubber, etc). The origin of the waste must be known.
No C&D waste from constructions, polluted with inorganic or organic dangerous substances, e.g. because of production
processes in the construction, soil pollution, storage and usage of pesticides or other dangerous substances, etc, unless it is
made clear that the demolished construction was not significantly polluted
No C&D waste from constructions, treated, covered or painted with materials, containing dangerous substances in significant
amounts

Waste not appearing on this list must be subject to testing as laid down under section 1 of this document to
determine if it fulfils the criteria for waste acceptable at landfills for inert waste as set out in section 2.1.2.

2.1.2.

Limit values for waste acceptable at landfills for inert waste

2.1.2.1. L e a c h i n g l i m i t v a l u e s

The following leaching limit values apply for waste acceptable at landfills for inert waste, calculated at liquid to
solid ratios (L/S) of 2 l/kg and 10 l/kg for total release and directly expressed in mg/l for C0 (the first eluate of
percolation test at L/S = 0,1 l/kg). Member States shall determine which of the test methods and corresponding
limit values in the table should be used.

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Component

L/S = 2 l/kg
mg/kg dry substance

L/S = 10 l/kg
mg/kg dry substance

C0 (percolation test)
mg/l

As

Ba

Cd

Cr

Cu

Hg

Mo

Ni

Pb

Sb

Se

Zn

Chloride

Fluoride

Sulphate

Phenol index

DOC (2)

TDS (3)

0,1

7

0,03

0,2

0,9

0,003

0,3

0,2

0,2

0,02

0,06

2

550

4

560 (1)

0,5

240

2 500

0,5

20

0,04

0,5

2

0,01

0,5

0,4

0,5

0,06

0,1

4

800

10

0,06

4

0,02

0,1

0,6

0,002

0,2

0,12

0,15

0,1

0,04

1,2

450

2,5

1 000 (1)

1 500 (1)

1

500

4 000

0,3

160

(1) If the waste does not meet these values for sulphate, it may still be considered as complying with the acceptance criteria if
the leaching does not exceed either of the following values: 1 500 mg/l as C0 at L/S = 0,1 l/kg and 6 000 mg/kg at
L/S = 10 l/kg. It will be necessary to use a percolation test to determine the limit value at L/S = 0,1 l/kg under initial
equilibrium conditions, whereas the value at L/S = 10 l/kg may be determined either by a batch leaching test or by a
percolation test under conditions approaching local equilibrium.

(2) If the waste does not meet these values for dissolved organic carbon (DOC) at its own pH value, it may alternatively be
tested at L/S = 10 l/kg and a pH between 7.5 and 8.0. The waste may be considered as complying with the acceptance
criteria for DOC, if the result of this determination does not exceed 500 mg/kg (A draft method based on prEN 14429 is
available).

(3) The values for TDS (Total Dissolved Solids) can be used alternatively to the values for Sulphate and Chloride.

2.1.2.2. L i m i t v a l u e s f o r t o t a l c o n t e n t o f o r g a n i c p a r a m e t e r s

In addition to the leaching limit values under section 2.1.2.1, inert wastes must meet the following additional
limit values:

Parameter

TOC

BTEX

PCBs (7 congeners)

Mineral oil (C10 to C40)

PAHs

Value mg/kg

30 000 (1)

6

1

500

Member States to set limit value

(1) In the case of soils a higher limit value may be admitted by the competent authority, provided the Dissolved Organic

Carbon at pH 7 (DOC7) value of 500 mg/kg is achieved.

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2.2.

Criteria for landfills for non-hazardous waste

Member States may create subcategories of landfills for non-hazardous waste.

In this annex limit values are only laid down for non-hazardous waste, which is landfilled in the same cell with
stable, non-reactive hazardous waste.

2.2.1. Wastes acceptable at landfills for non-hazardous waste without testing

Municipal waste as defined in Article 2(b) of Directive 1999/31/EC that is classified as non-hazardous in
Chapter 20 of the European Waste List, separately collected non-hazardous fractions of household wastes
and the same non-hazardous materials from other origins can be admitted without testing at landfills for
non-hazardous waste.

The wastes may not be admitted if they have not been subjected to prior treatment according to Article 6(a) of
Directive 1999/31/EG, or if they are contaminated to an extent which increases the risk associated with the
waste sufficiently to justify their disposal in other facilities.

They may not be accepted in cells, where stable, non-reactive hazardous waste is accepted pursuant to Article
6(c) iii) of Directive 1999/31/EC.

2.2.2.

Limit values for non-hazardous waste

The following limit values apply to granular non-hazardous waste accepted in the same cell as stable,
non-reactive hazardous waste, calculated at L/S = 2 and 10 l/kg for total release and directly expressed in
mg/l for C0 (in the first eluate of percolation test at L/S = 0,1 l/kg). Granular wastes include all wastes that are
not monolithic. Member States shall determine which of the test methods and corresponding limit values in the
table should be used.

Components

L/S = 2 l/kg
mg/kg dry substance

L/S = 10 l/kg
mg/kg dry substance

C0 (percolation test)
mg/l

As

Ba

Cd

Cr total

Cu

Hg

Mo

Ni

Pb

Sb

Se

Zn

Chloride

Fluoride

Sulphate

DOC (1)

TDS (2)

0,4

30

0,6

4

25

0,05

5

5

5

0,2

0,3

25

10 000

60

10 000

380

40 000

2

100

1

10

50

0,2

10

10

10

0,7

0,5

50

15 000

150

20 000

800

60 000

0,3

20

0,3

2,5

30

0,03

3,5

3

3

0,15

0,2

15

8 500

40

7 000

250

(1) If the waste does not meet these values for dissolved organic carbon (DOC) at its own pH, it may alternatively be tested at
L/S = 10 l/kg and a pH of 7.5 — 8.0. The waste may be considered as complying with the acceptance criteria for DOC, if
the result of this determination does not exceed 800 mg/kg (A draft method based on prEN 14429 is available).

(2) The values for TDS (Total Dissolved Solids) can be used alternatively to the values for Sulphate and Chloride.

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2.2.3. Gypsum Waste

Non-hazardous gypsum-based materials should only be disposed of in landfills for non-hazardous waste in cells
where no biodegradable waste is accepted. The limit values for Total Organic Carbon (TOC) and Dissolved
Organic Carbon at pH 7 (DOC7) given in section 2.3.2 shall apply to wastes landfilled together with
gypsum-based materials.

2.3.

Criteria for hazardous waste acceptable at landfills for non-hazardous waste pursuant to Article 6(c)(iii)

Stable, non-reactive means that the leaching behaviour of the waste will not change adversely in the long-term,
under landfill design conditions or foreseeable accidents:

— in the waste alone (for example, by biodegradation);

— under the impact of long-term ambient conditions (for example, water, air, temperature, mechanical

constraints);

— by the impact of other wastes (including waste products such as leachate and gas).

2.3.1.

Leaching limit values

The following leaching limit values apply to granular hazardous waste acceptable at landfills for non-hazardous
waste, calculated at L/S = 2 and 10 l/kg for total release and directly expressed in mg/l for C0 (the first eluate of
percolation test at L/S = 0,1 l/kg). Granular wastes include all wastes that are not monolithic. Member States
shall determine which of the test methods and corresponding limit values should be used.

Components

L/S = 2 l/kg
mg/kg dry substance

L/S = 10 l/kg
mg/kg dry substance

C0 (percolation test)
mg/l

As

Ba

Cd

Cr total

Cu

Hg

Mo

Ni

Pb

Sb

Se

Zn

Chloride

Fluoride

Sulphate

DOC (1)

TDS (2)

0,4

30

0,6

4

25

0,05

5

5

5

0,2

0,3

25

10 000

60

10 000

380

40 000

2

100

1

10

50

0,2

10

10

10

0,7

0,5

50

15 000

150

20 000

800

60 000

0,3

20

0,3

2,5

30

0,03

3,5

3

3

0,15

0,2

15

8 500

40

7 000

250

(1) If the waste does not meet these values for dissolved organic carbon (DOC) at its own pH, it may alternatively be tested at
L/S = 10 l/kg and a pH of 7.5 — 8.0. The waste may be considered as complying with the acceptance criteria for DOC, if
the result of this determination does not exceed 800 mg/kg (A draft method based on prEN 14429 is available).

(2) The values for TDS (Total Dissolved Solids) can be used alternatively to the values for Sulphate and Chloride.

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Member States must set criteria for monolithic waste to provide the same level of environmental protection
given by the above limit values.

2.3.2. Other criteria

In addition to the leaching limit values under section 2.3.1, granular wastes must meet the following additional
criteria:

Parameter

TOC

PH

ANC

Value

5 % (1)

minimum 6

Must be evaluated

(1) If this value is not achieved, a higher limit value may be admitted by the competent authority, provided that the Dissolved

Organic Carbon (DOC) value at pH7 of 800 mg/kg is achieved.

Member States must set criteria to ensure that the waste will have sufficient physical stability and bearing
capacity.

Member States must set criteria to ensure that hazardous monolithic wastes are stable and non-reactive before
acceptance in landfills for non-hazardous waste.

2.3.3. Asbestos waste

Construction materials containing asbestos and other suitable asbestos waste may be landfilled at landfills for
non-hazardous waste in accordance with Article 6(c)(iii) of Directive 1999/31/EC without testing.

For landfills receiving construction materials containing asbestos and other suitable asbestos waste the following
requirements must be fulfilled:

— The waste contains no other hazardous substances than bound asbestos,

including fibres bound by a

binding agent or packed in plastic.

— The landfill accepts only construction material containing asbestos and other suitable asbestos waste. These
is

wastes may also be landfilled in a separate cell of a landfill for non-hazardous waste,
sufficiently self-contained.

if the cell

— In order to avoid dispersion of fibres, the zone of deposit is covered daily and before each compacting

operation with appropriate material and, if the waste is not packed, it is regularly sprinkled.

— A final top cover is put on the landfill/cell in order to avoid the dispersion of fibres.

— No works are carried out on the landfill/cell that could lead to a release of fibres (e.g. drilling of holes).

— After closure a plan is kept of the location of the landfill/cell indicating that asbestos wastes have been

deposited.

— Appropriate measures are taken to limit the possible uses of the land after closure of the landfill in order to

avoid human contact with the waste.

For landfills receiving only construction material containing asbestos, the requirements set out in Annex I, point
3.2 and 3.3 of Directive 1999/31/EC can be reduced, if the above requirements are fulfilled.

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2.4.

Criteria for waste acceptable at landfills for hazardous waste

2.4.1.

Leaching limit values

The following leaching limit values apply for granular waste acceptable at landfills for hazardous waste,
calculated at L/S = 2 and 10 l/kg for total release and directly expressed in mg/l for C0 (in the first eluate
of percolation test at L/S = 0,1 l/kg) Granular wastes include all wastes that are not monolithic. Member States
shall determine which of the test methods and corresponding limit values in the table should be used.

Components

L/S = 2 l/kg
mg/kg dry substance

L/S = 10 l/kg
mg/kg dry substance

C0 (percolation test)
mg/l

As

Ba

Cd

Cr total

Cu

Hg

Mo

Ni

Pb

Sb

Se

Zn

Chloride

Fluoride

Sulphate

DOC (1)

TDS (2)

6

100

3

25

50

0,5

20

20

25

2

4

90

17 000

200

25 000

480

70 000

25

300

5

70

100

2

30

40

50

5

7

200

25 000

500

50 000

1 000

100 000

3

60

1,7

15

60

0,3

10

12

15

1

3

60

15 000

120

17 000

320

(1) If the waste does not meet these values for dissolved organic carbon (DOC) at its own pH, it may alternatively be tested at
L/S = 10 l/kg and a pH of 7.5 — 8.0. The waste may be considered as complying with the acceptance criteria for DOC, if
the result of this determination does not exceed 800 mg/kg (A draft method based on prEN 14429 is available).

(2) The values for TDS (Total Dissolved Solids) can be used alternatively to the values for Sulphate and Chloride.

Member States shall set criteria for monolithic waste to provide the same level of environmental protection
given by the above limit values.

2.4.2. Other criteria

In addition to the leaching limit values under section 2.4.1, hazardous wastes must meet the following
additional criteria:

Parameter

LOI (Loss on Ignition) (1)

TOC (Total Organic Carbon) (1)

Values

10 %

6 % (2)

ANC (Acid Neutralisation Capacity)

Must be evaluated

(1) Either LOI or TOC must be used.
(2) If this value is not achieved, a higher limit value may be admitted by the competent authority, provided that the DOC pH7

value of 1 000 mg/kg is achieved.

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2.5.

Criteria for underground storage

For the acceptance of waste in underground storage sites a site specific safety assessment as defined in Annex A
to this document must be carried out. Waste may only be accepted, if it is compatible with the site-specific
safety assessment.

At underground storage sites for inert waste only waste that fulfils the criteria set out in section 2.1 may be
accepted.

At underground storage sites for non-hazardous waste only waste that fulfils the criteria set out in section 2.2
or in section 2.3 may be accepted.

At underground storage sites for hazardous waste, waste may only be accepted, if it is compatible with the
site-specific safety assessment. In this case the criteria set out in section 2.4 do not apply. However, the waste
must be subject to the acceptance procedure as set out in section.

3.

SAMPLING AND TEST METHODS

Sampling and testing shall be carried out by independent and qualified persons and institutions. Laboratories
shall have proven experience in waste testing and analysis an an efficient quality assurance system.

The following methods shall be used:

Sampling

For the sampling of waste — for basic characterisation, compliance testing and on-site verification testing- a
sampling plan shall be developed according to part 1 of the sampling standard currently developed by CEN. As
long as the CEN standard is not available as formal EN, Member States will use either national standards or the
draft CEN standard, when it has reached the prEN stage.

General waste properties

EN 13137

Determination of Total Organic Carbon (TOC) in waste, sludge and sediments

prEN 14346

Calculation of dry matter by determination of dry residue or water content

Leaching tests

prEN 14405

Leaching behaviour test — Up-flow percolation test (Up-flow percolation test for
inorganic constituents)

EN 12457/1-4

Leaching- Compliance test
for leaching of granular waste materials and sludges
(Compliance leaching test for granular waste L/S 2, 4 mm; L/S 10, 4 mm; L/S 2 and
8, 4 mm; L/S 10, 10 mm)

Digestion of raw waste

EN 13657

EN 13656

Digestion for subsequent determination of aqua regia soluble portion of elements
(Partial digestion of the solid waste prior to elementary analysis, leaving the silicate
matrix intact)

Microwave assisted digestion with hydrofluoric (HF), nitric (HNO3) and hydrochloric
(HCl) acid mixture for subsequent determination of elements (Total digestion of the
solid waste prior to elementary analysis)

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Analysis

ENV 12506

ENV 13370

Analysis of eluates — Determination of pH, As, Ba, Cd, Cl, Co, Cr, CrVI, Cu, Mo, Ni,
No2, Pb, total S, SO4, V and Zn (Analysis of inorganic constituents of solid waste
and/or its eluate;major, minor and trace elements)

Analysis of eluates — Determination of Ammonium, AOX, conductivity, Hg, phenol
index, TOC, easily liberatable CN, F (Analysis of inorganic constituents of solid waste
and/or its eluate (anions))

prEN 14039

Determination of hydrocarbon content in the range of C10-C40 by gas chroma-
tography

This list will be amended when more CEN standards are available.

For tests and analyses, for which CEN methods are not (yet) available, the methods used must be approved by
the competent authorities.

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SAFETY ASSESSMENT FOR ACCEPTANCE OF WASTE IN UNDERGROUND STORAGE

Annex A

1.

SAFETY PHILOSOPHY FOR UNDERGROUND STORAGE: ALL TYPES

1.1.

The Importance of the Geological Barrier

Isolation of wastes from the biosphere is the ultimate objective for the final disposal of wastes in underground
storage. The wastes, the geological barrier and the cavities,
including any engineered structures constitute a
system that together with all other technical aspects must fulfil the corresponding requirements.

The requirements of the Water Framework Directive (2000/60/EC) can only be fulfilled by demonstrating the
long term safety of the installation (see section 2.2.5 below). Article 11 para 3 (j) of Directive 2000/60/EC
generally prohibits the direct discharge of pollutants into groundwater. Article 4 para 1 (b) (i) of Directive
2000/60/EC requires Member States to take measures to prevent the deterioration of the status of all bodies
of groundwater.

1.2.

Site Specific Risk Assessment

The Assessment of risk requires the identification of:

— the hazard (in this case the deposited wastes),

— the receptors (in this case the biosphere and possibly groundwater),

— the pathways by which substances from the wastes may reach the biosphere, and

— the assessment of impact of substances that may reach the biosphere.

Acceptance criteria for underground storage are to be derived from, inter alia, the analysis of the host rock, so it
must be confirmed that no site-related conditions specified in Annex I of the Landfill Directive (with an
exemption of Annex I paragraph 2, 3, 4 and 5) have relevance.

The acceptance criteria for underground storage can only be obtained by referring to the local conditions. This
requires a demonstration of the suitability of the strata for establishing a storage, i.e. an assessment of the risks to
containment, taking into account the overall system of the waste, engineered structures and cavities and the host
rock body.

The site specific risk assessment of the installation must be carried out for both the operational and post
operational phases. From these assessments, the required control and safety measures can be derived and the
acceptance criteria can be developed.

An integrated performance assessment analysis shall be prepared, including the following components:

1. geological assessment

2. geomechanical assessment

3. hydrogeological assessment

4. geochemical assessment

5. biosphere impact assessment

6. assessment of the operational phase

7.

long-term assessment

8. assessment of the impact of all the surface facilities at the site

1.2.1. Geological Assessment

A thorough investigation or knowledge of the geological setting of a site is required. This includes investigations
and analyses of kind of rocks, soils and the topography. The geological assessment should demonstrate the
suitability of the site for underground storage. The location, frequency and structure of any faulting or fracturing
in surrounding geological strata and the potential
impact of seismic activity on these structures should be
included. Alternative site locations should be considered.

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1.2.2. Geomechanical assessment

The stability of the cavities must be demonstrated by appropriate investigations and predictions. The deposited
waste must be part of this assessment. The processes should be analysed and documented in a systematic way.

The following should be demonstrated:

1. that during and after the formation of the cavities, no major deformation is to be expected either in the cavity
itself or at the earth surface which could impair the operability of the underground storage or provide a
pathway to the biosphere,

2. that the load bearing capacity of the cavity is sufficient to prevent its collapse during operation,

3. that the deposited material must have the necessary stability compatible with the geo- mechanical properties

of the host rock.

1.2.3. Hydrogeological Assessment

A thorough investigation of the hydraulic properties is required to assess the groundwater flow pattern in the
surrounding strata based on information on the hydraulic conductivity of the rock mass, fractures and the
hydraulic gradients.

1.2.4. Geochemical Assessment

A thorough investigation of the rock and the groundwater composition is required to assess the present
groundwater composition and its potential evolution over time, the nature and abundance of fracture filling
minerals, as well as a quantitative mineralogical description of the host rock. The impact of variability on the
geochemical system should be assessed.

1.2.5. Biosphere Impact Assessment

An investigation of the biosphere that could be impacted by the underground storage is required. Baseline studies
should be performed to define local natural background levels of relevant substances.

1.2.6. Assessment of the Operational Phase

For the operational phase the analysis should demonstrate the following:

1. the stability of the cavities as in 1.2.2 above;

2. there is no unacceptable risk of a pathway developing between the wastes and the biosphere;

3. there are no unacceptable risks affecting the operation of the facility.

When demonstrating operational safety, a systematic analysis of the operation of the facility must be made on the
basis of specific data on the waste inventory, facility management and the scheme of operation. It is to be shown
that the waste will not react with the rock in any chemical or physical way, which could impair the strength and
tightness of the rock and endanger the storage itself. For these reasons, in addition to wastes that are banned by
Article 5.3 of the Directive, wastes that are liable to spontaneous combustion under the storage conditions
(temperature, humidity), gaseous products, volatile wastes, wastes coming from collections in the form of
unidentified mixtures should not be accepted.

Particular incidents that might lead to the development of a pathway between the wastes and the biosphere in the
operational phase should be identified. The different types of potential operational risks should be summarized in
specific categories. Their possible effects should be evaluated. It should be shown that there is no unacceptable
risk that the containment of the operation will be breached. Contingency measures should be provided.

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1.2.7. Long-term Assessment

In order to comply with the objectives of sustainable landfilling, risk assessment should cover the long-term. It
must be ascertained that no pathways to the biosphere will be generated during the long-term post-operation of
the underground storage.

The barriers of the underground storage site (e.g. the waste quality, engineered structures, back filling and sealing
of shafts and drillings), the performance of the host rock, the surrounding strata and the overburden should be
quantitatively assessed over the long-term and evaluated on the basis of site-specific data or sufficiently conser-
vative assumptions. The geochemical and geohydrological conditions such as groundwater flow (see section 1.2.3
and 1.2.4 above), barrier efficiency, natural attenuation as well as leaching of the deposited wastes should be
taken into consideration.

The long-term safety of an underground storage should be demonstrated by a safety assessment comprising a
description of the initial status at a specified time (e.g. time of closure) followed by a scenario outlining important
changes that are expected over geological time. Finally the consequences of the release of relevant substances
from the underground storage should be assessed for different scenarios reflecting the possible long-term
evolution of the biosphere, geosphere and the underground storage.

Containers and cavity lining should not be taken into account when assessing the long-term risks of waste
deposits because of their limited lifetime.

1.2.8. Impact Assessment of the Surface Reception Facilities

Although the wastes taken at the site may be destined for subsurface disposal, wastes will be unloaded, tested and
possibly stored on the surface, before reaching their final destination. The reception facilities must be designed
and operated in a manner that will prevent harm to human health and the local environment. They must fulfil
the same requirements as any other waste reception facility.

1.2.9. Assessment of other Risks

For reasons of protection of labourers, wastes should only be deposited in an underground storage securely
separated from mining activities. Waste should not be accepted if it contains or could generate hazardous
substances which might harm human health, e.g. pathogenic germs of communicable diseases.

2.

ACCEPTANCE CRITERIA FOR UNDERGROUND STORAGE: ALL TYPES

2.1.

Excluded wastes

In the light of sections 1.2.1-1.2.8 above, wastes that may undergo undesired physical, chemical or biological
transformation after they have been deposited must not be disposed of in underground storage. This includes the
following:

(a) Wastes listed in Article 5.3 of the Directive

(b) Wastes and their containers which might react with water or with the host rock under the storage conditions

and lead to:

— a change in the volume;

— generation of auto-flammable or toxic or explosive substances or gases; or

— any other reactions which could endanger the operational safety and/or the integrity of the barrier.

Waste which might react with each other must be defined and classified in groups of compatibility; the
different groups of compatibility must be physically separated in the storage.

(c) Wastes that are biodegradable.

(d) Wastes that have a pungent smell.

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(e) Waste that can generate a gas-air mixture which is toxic or explosive. This particularly refers to wastes that:

— cause toxic gas concentrations due to the partial pressures of their components;

— form concentrations when saturated within a container, which are higher than 10 % of the concentration

which corresponds to the lower explosive limit.

(f) Wastes with insufficient stability to correspond to the geomechanical conditions.

(g) Wastes that are auto-flammable or liable to spontaneous combustion under the storage conditions, gaseous

products, volatile wastes, wastes coming from collections in the form of unidentified mixtures.

(h) Wastes that contain or could generate pathogenic germs of communicable diseases (already provided for by

Article 5(3)(c) of the Directive).

2.2.

Lists of waste suitable for underground storage

Inert wastes, hazardous and non-hazardous wastes, not excluded by 2.1 and 2.2 above may be suitable for
underground storage.

Member States may produce lists of wastes acceptable at underground storage facilities in accordance with the
classes given in Article 4 of the Directive.

2.3.

Site specific risk assessment

Acceptance of waste at a specific site must be subject to site-specific risk assessment.

The site-specific assessments outlined in section 1.2 above for the wastes to be accepted at an underground
storage should demonstrate that the level of isolation from the biosphere is acceptable. The criteria have to be
fulfilled under storage conditions.

2.4. Acceptance conditions

Wastes can only be deposited in an underground storage securely separated from mining activities.

Wastes that might react with each other must be defined and classified in groups of compatibility; the different
groups of compatibility must be physically separated in the storage.

3.

ADDITIONAL CONSIDERATIONS: SALT MINES

3.1.

Importance of the Geological Barrier

In the safety philosophy for salt mines, the rock surrounding the waste has a two-fold role:

— It acts as host rock in which the wastes are encapsulated.

— Together with the over and underlying impermeable rock strata (e.g. anhydrite), it acts as a geological barrier
intended to prevent groundwater entering the landfill and, where necessary, to effectively stop liquids or gases
escaping from the disposal area. Where this geological barrier is pierced by shafts and boreholes, these must
be sealed during operation to secure against ingress of water, and must be hermetically closed after the
underground landfill ceases to operate. If mineral extraction continues longer than the landfill operation, the
disposal area must, after the landfill has ceased operating, be sealed with a hydraulically impermeable dam
which is constructed according to the calculated hydraulically operative pressure corresponding to the depth,
so that water which may seep into the still operating mine cannot penetrate through to the landfill area.

— In salt mines, the salt is considered to provide total containment. The wastes will only make contact with the
biosphere in the case of an accident or an event in geological time such as earth movement or erosion (for
example, associated with sea-level rise). The waste is unlikely to change in storage, and the consequences of
such failure scenarios must be considered.

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3.2.

Long term assessment

The demonstration of long-term safety of underground disposal in a salt rock should be principally undertaken
by designating the salt rock as the barrier rock. Salt rock fulfils the requirement to be impermeable to gases and
liquids, to be able to encase the waste because of its convergent behaviour and to confine it entirely at the end of
the transformation process. The convergent behaviour of the salt rock thus does not contradict the requirement
to have stable cavities in the operation phase. The stability is important, in order to guarantee the operational
safety and in order to maintain the integrity of the geological barrier over unlimited time, so that there is
continued protection of the biosphere. The wastes should be isolated permanently from the biosphere. Controlled
subsidence of the overburden or other defects over long time are only acceptable if it can be shown, that only
rupture-free transformations will occur, the integrity of the geological barrier is maintained and no pathways are
formed by which water would be able to contact the wastes or the wastes or components of the waste migrate to
the biosphere.

4.

ADDITIONAL CONSIDERATIONS: HARD-ROCK

Deep storage in hard rock is here defined as an underground storage at several hundred meters depth, where hard
rock includes various igneous rocks, e.g. granite or gneiss, it may also include sedimentary rocks, e.g. limestone
and sandstone.

4.1.

Safety philosophy

A deep storage in hard rock is a feasible way to avoid burdening future generations with the responsibility of the
wastes since it should be constructed to be passive and with no need for maintenance. Furthermore, the
construction should not obstruct recovery of the wastes or the ability to undertake future corrective measures.
It should also be designed to ensure that negative environmental effects or liabilities resulting from the activities
of present generations would not fall upon future generations.

In the safety philosophy of underground disposal of wastes the main concept is isolation of the waste from the
biosphere, as well as natural attenuation of any pollutants leaking from the waste. For certain types of hazardous
substances and waste a need has been identified to protect the society and the environment against sustained
exposure over extended periods of time. An extended period of time implies several thousands of years. Such
levels of protection can be achieved by deep storage in hard rock. A deep storage for waste in hard rock can be
located either in a former mine, where the mining activities have come to an end, or in a new storage facility.

In the case of hard-rock storage, total containment is not possible. In this case, an underground storage needs to
be constructed so that natural attenuation of the surrounding strata mediates the effect of pollutants to the extent
that they have no irreversible negative effects on the environment. This means that the capacity of the near
environment to attenuate and degrade pollutants will determine the acceptability of a release from such a facility.

The requirements of the EU Water Framework Directive (2000/60/EC) can only be fulfilled by demonstrating the
long-term safety of the installation (see 1.2.7 above). The performance of a deep storage system must be assessed
in a holistic way, accounting for the coherent function of different components of the system. In a deep storage
in hard rock the storage will reside below the groundwater table. Article 11 paragraph 3 (j) of the Directive
generally prohibits the direct discharge of pollutants into groundwater. Article 4 paragraph 1 (b) (i) of the
Directive requires Member States to take measures to prevent the deterioration of the status of all bodies of
groundwater. For a deep storage in the hard rock this requirement is respected in that any discharges of
hazardous substances from the storage will not reach the biosphere, including the upper parts of the groundwater
system accessible for the biosphere, in amounts or concentrations that will cause adverse effects. Therefore the
water flow paths to and in the biosphere should be evaluated. The impact of variability on the geohydraulic
system should assessed.

Gas formation may occur in deep storage in hard rock due to long-term deterioration of waste, packaging and
engineered structures. Therefore, this must be considered in the design of premises for a deep storage in hard
rock.

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OVERVIEW OF LANDFILLING OPTIONS PROVIDED BY THE LANDFILL DIRECTIVE

Annex B

Introduction

Figure 1 gives an overview of the landfilling possibilities for waste provided by the Landfill Directive (LFD) together with
some examples of sub-categories of the main classes of landfills. The starting point (upper left corner) is a waste, which
should be landfilled. In accordance with article 6(a), some treatment is required prior to landfilling for most wastes. The
general definition of ‘treatment’ is relatively broad and to a large extent left to the competent authorities in the Member
States. It is assumed that the waste does not belong to any of the categories listed in article 5.3 of the Directive.

Inert waste landfill

The first question to ask could be whether or not the waste is classified as hazardous. If the waste is not hazardous
(according to the Hazardous Waste Directive and the current Waste List), the next question could be whether or not the
waste is inert. If it meets the criteria for waste to be landfilled at an inert landfill (class A, see figure 1 and table 1), the
waste may be placed at an inert landfill.

Inert waste may alternatively be placed in landfills for non-hazardous waste provided it fulfils the appropriate criteria
(which it generally should).

Non-hazardous waste landfill, including sub-categories

If the waste is neither hazardous nor inert, then it must be non-hazardous, and it should go to a landfill for
non-hazardous waste. Member States may define sub-categories of landfills for non-hazardous waste in accordance
with their national waste management strategies as long as the requirements of the LFD are met. Three major
sub-categories of non-hazardous waste landfills are shown in figure 1: landfill for inorganic waste with low organic/
biodegradable content (B1), landfill for organic waste (B2), and landfill for mixed non-hazardous waste with substantial
contents of both organic/biodegradable and inorganic materials. Category B1 sites can be subdivided further into sites
for wastes that do not meet the criteria set out in section 2.2.2 of this decision document for inorganic non-hazardous
wastes that may be co-disposed with stable, non reactive hazardous wastes (B1a) and sites for wastes that do meet those
criteria (B1b). Category B2 sites may e.g. be further subdivided into bioreactor landfills and landfills for less reactive,
biologically treated waste. Further sub-classification of non-hazardous landfills may be desired by some Member States,
and monofills and landfills for solidified/monolithic waste may be defined within each subcategory (see the footnote
below table 1). National acceptance criteria may be developed by the Member States to ensure proper allocation of
sub-classification of
non-hazardous waste to the various
non-hazardous waste landfills is not desired, all non-hazardous waste (subject of course to the provisions of articles
3 and 5 of the Landfill Directive) may go to a landfill for mixed non-hazardous waste (class B3).

sub-categories of non-hazardous waste landfills.

If

Placement of stable, non-reactive hazardous waste in landfill for non-hazardous waste

If the waste is hazardous (according to the Hazardous Waste Directive and the current Waste List), the treatment may
have enabled the waste to meet the criteria for placement of stable, non-reactive hazardous waste in non-hazardous
waste landfills within cells for inorganic waste with low organic/biodegradable content that meet the criteria in Section
2.2.2 of this decision document (class B1b). The waste may be granular (rendered chemically stable) or solidified/mono-
lithic.

Hazardous waste landfill

If the hazardous waste does not meet the criteria for placement in a class B1b landfill or cell for non-hazardous waste,
the next question could be whether or not it meets the criteria for acceptance at a landfill for hazardous waste (class C,
see below). If the criteria are met, then the waste may be placed at a hazardous waste landfill.

If the criteria for acceptance at a hazardous waste landfill are not met, then the waste may be subjected to further
treatment and tested again against the criteria, until they are met.

Underground storage

Alternatively, the waste may be tested against the criteria for underground storage. If the criteria are met, the waste may
go to an underground storage facility for hazardous waste (landfill class DHAZ). If the underground storage criteria are
not met, the waste may be subjected to further treatment and tested again.

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Although underground storage is likely to be reserved for special hazardous wastes, this sub-category may in principle
be used also for inert waste (class DINERT) and non-hazardous waste (class DNON-HAZ).

Figure 1: Diagram showing the landfilling options provided by the Landfill Directive.

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Table 1

Overview of landfill classes and examples of sub-categories

Landfill Class

Major sub-categories

ID

Acceptance criteria

(underground storage facilities, monofills and
landfills for
solidified, monolithic (*) waste
possible for all landfill classes)

Landfill for inert waste

Landfill accepting inert waste

A

for

leaching

Criteria
content of organic
and for
components are set at EU level (2.1.2 of this document)
Criteria for content of inorganic components may be set at
MS level

Landfill
for inorganic non-hazardous waste
with a low content of organic/bio-degradable
matter, where the wastes do not meet the
criteria set out
in section 2.2.2 for those
inorganic non-hazardous wastes that may be
landfilled together with stable, non-reactive
hazardous waste

B1a

Criteria for leaching and total content are not set at EU
level

Landfill
waste

for non-hazardous

Landfill
for inorganic non-hazardous waste
with a low content of organic/bio-degradable
matter

B1b

Criteria for leaching and content of organics (TOC) and
other properties are set at EU level, common for granular
non-reactive
non-hazardous waste
hazardous waste (section 2.2). Additional stability criteria
for the latter are to be set at MS level. Criteria for mono-
lithic waste must be set at MS level

stable,

and

for

Landfill for organic non-hazardous waste

B2

Criteria for leaching and total content are not set at EU
level

Landfill for mixed non-hazardous waste with
substantial contents of both organic/biode-
gradable waste and inorganic waste

Surface landfill for hazardous waste

B3

C

Criteria for leaching and total content are not set at EU
level

Criteria for leaching for granular hazardous waste and
total content of certain components have been laid
down at EU level
(section 2.4). Criteria for monolithic
waste must be set at MS level.
Additional criteria on content of contaminants can be set
at MS level

Landfill for hazardous waste

Underground storage site

DHAZ

Special requirements at EU level are listed in Annex A

(*) Monolithic waste subcategories are only relevant for B1, C and DHAZ and possibly A. MS = EU Member States.