A framework for regional high-level technical screening of promising CCUS value chains

Abstract

To support the European Green Deal and accelerate climate mitigation, the CCUS ZEN project conducted a high-level technical screening of Carbon Capture, Utilization, and Storage (CCUS) value chains in the Baltic and Mediterranean regions. These regions were chosen, since they have lower maturity levels for CCUS compared with the current development in the North Sea region. The study mapped industrial carbon dioxide (CO₂) emission sources, potential storage sites, transport infrastructure, and utilization options. Emission clusters and hubs were identified based on volume, location, and industry type, while for each mapped storage site, information was gathered about the type of reservoir (deep saline aquifer or depleted hydrocarbon field), the onshore or offshore location, the capacity of the reservoir and the Storage Readiness Level, indicating the maturity of the capacity evaluation. Transport options included pipelines, shipping, and multimodal solutions were presented. This study defined unique high-level technical CCUS value chain screening workflow for mapping of emitters, infrastructures to storage screening. An open geographical information system was used for mapping the emitters and storage sites from previous reports, and to illustrate emission clusters and possible transport routes, both existing and future infrastructures. The screening revealed significant CO₂ emission sources and storage capacities across the regions, with notable clusters in Poland, Germany, Italy, and Turkey. The Baltic region showed three times the storage capacity of the Mediterranean region. Eight promising CCUS value chains were defined, integrating source-sink matching and infrastructure feasibility. A detailed case study of Southern Italy and Greece was presented, to demonstrate the potential for regional CCUS deployment, highlighting challenges such as data availability, storage capacity uncertainty, transport possibilities and stakeholder coordination. This study will provide a foundation for further development and stakeholder engagement in CCUS planning across Europe.

1 Introduction

There is a strong ambition to accelerate the deployment of Carbon, Capture, Utilization, and Storage (CCUS) throughout Europe, as a part of the European Green Deal (European Commission, 2019), the European Climate Law and to increase climate energy and climate targets for 2030 (Tumara et al., 2024). As part of this, the EU funded network project CCUS ZEN has connected CCUS actors in Europe, to identify promising value chains and to share knowledge and experience. We carried out a high-level technical mapping focused on emission sources, storage sites, transport infrastructure, utilization options and renewables, alongside non-technical mapping including stakeholder needs, regulations, climate policies and funding opportunities (Figure 1). These aspects should be considered when CCUS value chain are to be developed further after the initial technical high-level screening. One of the objectives was to explore the potential for CCUS value chain deployment in two regions with lower maturity level for CCUS compared to the current development in the North Sea region. A high-level screening of promising value chains has been carried out for two selected regions: the Baltic Sea region and the Mediterranean Sea region (Ringstad et al., 2023). The overall screening workflow was tested in the two geographical regions, with different geological storage sites (aquifers and depleted oil and gas fields) and led to the definition of 8 CCUS value chains, several with different transport solutions included, using ships or pipelines or a combination (Gravaud et al., 2024).

FIGURE 1

2 Methodology and input data for high-level CCUS technical value chain screening

Several studies have been carried out focusing on high-level CCUS value chain screening with scenario developments (Jakobsen and Brunsvold, 2011), infrastructures (Kjärstad and Johnsson, 2009; European Commission, 2024) and storage sites (Anthonsen et al., 2014a; Anthonsen et al., 2014b). The high-level CCUS technical value chain can be subdivided into four main parts covering mapping of CO₂ emitters, infrastructure screening, storage sites screening and utilization as a final part in the puzzle (Lothe et al., 2025) (see Figure 2). For each part of the value chain, several key input parameters are listed without ranking the importance, costs, or effort to get enough data to draw solid conclusions.

FIGURE 2

As part of the high-level CCUS technical screening, an open geographical information system (QGIS) has been used for mapping the emitters and storage sites from previous reports, and to illustrate emission clusters and possible transport routes, both existing and future infrastructures. The aim is to carry out a first qualitative high-level screening, a more quantitative assessment of potential CCUS value chains are presented by Shogenova et al. (2025).

2.1 Mapping of emitters

Inspection of the emission sources in each geographical region leads to the identification of promising sites for CO₂ capture. The focus is on identifying clusters of emitters, where CO₂ could be captured from different industrial sites and gathered at a hub before the transport to storage. Standalone emitters could also be identified as promising for CCUS value chains, depending on their amount of emission, location, and type of industry. For each emission source, information about the facility is collected (facility name, company, location, coordinates, and industrial sector), along with information about the facility’s emissions (annual amount of CO₂ emitted, emissions trend, share of biomass, and waste-to-energy) (see Table 1).

The CO₂ emission database in CaptureMap, provided by Endrava is sourced from the EU Emissions Trading System (EU-ETS) and the European Pollutant Release and Transfer Register (E-PRTR). The EU-ETS data mainly includes fossil-based CO₂ emissions, whereas the E-PRTR includes both fossil-based and biogenic CO₂ emissions. The E-PRTR dataset only includes the facilities with CO₂ emissions above 100 kt/y, while the EU-ETS dataset also includes the facilities with smaller emission volumes (<100 kt/y). Since CaptureMap uses the E-PRTR system as their basis for facilities in European countries, many facilities with CO₂ emissions less than 100 kt/y are not included in the database.

Data from CaptureMap were used for mapping CO₂ emissions sources in the Baltic Sea region (Denmark, Sweden, Finland, Germany, Estonia, Latvia, Lithuania and Poland) and the Mediterranean Sea region (France, Spain, Italy and Greece). The emission data were quality-checked, and amended where necessary, by the CCUS ZEN partners in Denmark, Sweden, Finland, Estonia, Latvia, Lithuania, Poland and France.

Since Turkey is not covered in the CaptureMap database, this emission mapping was carried out using methodology described in IPCC (2006), see also Ringstad et al. (2023). Due to the unavailability of annual, sector-based CO₂ emission data, the mapping of CO₂ emission sources in Turkey has been restricted to emissions from the leading sectors in terms of CO₂ emissions, namely, the refineries and petrochemical industry, power plants, iron and steel industry, and cement industry. The reported CO₂ emissions are in general from 2021, except for some facilities where only older data were available. Clusters are defined, with the total amount of emissions, the number of facilities in the cluster, and the share of each industrial sector in the total emissions.

2.2 Mapping of infrastructures

For the infrastructure screening, we looked at existing infrastructure relevant for CO₂-transport with emphasis on pipelines (onshore and offshore), existing natural gas corridors, waterways and ports. Existing pipelines could either be reused if they have the specifications needed (e.g., temperature and pressure limitations and material) or the pipeline corridor can be used as a route for a new CO₂ pipeline. If transport using pipelines or waterways is not an option, also railways and road (lorries) are evaluated.

There are multiple ways to transport CO₂ which include pipelines, ships, trucks/lorries or railways. All methods are often combined with pre- and/or post-processes such as compression and drying of the CO₂ stream, removal of impurities, liquefaction and intermediate storage solutions. Larger CO₂ quantities, such as usually expected for a CO₂ cluster require either a pipeline or ships, or a combination of both. This sub-section presents a high-level comparison between the two transportation methods.

The best transportation is often a combination of multiple methods that balance costs with convenience, practicality and in compliance with safety, legal and environmental requirements. Pipelines are commonly the most economical way to transport large quantities of CO₂ over short to medium distances. On the other hand, pipelines are not a temporary flexible infrastructure and must primarily be considered for long-term operations. They require a high initial investment, but reduced OPEX. Re-utilisation of existing infrastructure may, therefore, be a key for such projects. OPEX may also be reduced by combining processes like drying or compression with the emitter’s industrial processes which produce heat or cold. Construction of a CO₂ pipeline should consider the environmental impacts and routes may need to be adopted to minimize impact on protected areas. The risk to residential or densely populated areas may also need to be considered when planning CO₂ pipelines. Pipelines can transport CO₂ at gaseous, liquid or supercritical phases. Currently, there are approximately 8,000 km of onshore CO₂ pipeline in the US. In Norway, one offshore CO₂ 100-kilometres long pipeline has been built as part of the Northern Light project, from Øygarden to Aurora Field, and one 160-kilometre pipeline from Melkøya to the Snøhvit Field.

Shipping is a more flexible operation and is viable for longer distances but also for small volumes. While the capital expenditure (CapEx) costs are lower and the ships can be repurposed after the project closure, the operational expenditure (OpEx) costs are a main decision driver. Residential areas are not an obstacle in ship traffic and compliance to environmental restrictions is easier. On the other hand, ship-based transport is dependent on the existence of suitable harbours and is limited to the sea and waterways. Shipping logistics commonly require a large intermediate storage, and CO₂ can only be transported in liquid phase. Commonly today, 1,500–3,000 tonnes vessels are used in the food industry, and the transport conditions are 15 bar and −28°C. It is foreseen that the ship size for CCS project will be larger, but it depends on the logistic chain.

For transportation the mapping tool developed in the CO2LOS project was used to identify opportunities in ship transport or barges, while Project of Common Interest (PCI) Transparency Platform, combined with OpenStreetMap, was used for pipelines. Additionally, the European Network of Transmission Systems Operators for Gas (ENTSOG) provides a yearly updated map with an overview of existing gas pipeline infrastructure and projections for future development.

2.3 Mapping of storage sites

There are two main categories for underground carbon dioxide storage: saline aquifers and depleted oil and gas production reservoirs. Other geological storage options, like mineral carbonisation in basaltic rocks, were not considered, since such sites have not been mapped in detail.

The amount of CO₂ to be stored underground depends significantly on the media for the storage and the injectivity. The subsurface storage aquifers can be defined as a regional aquifer, a storage assessment unit, which has an upper limit defined by where the CO₂ will be in supercritical phase (approximately below 800 m depth, depending on pressures and temperature variations). The lower limit is defined by the porosity and permeability of the reservoir units and will be defined on what is considered an acceptable injection rate. This work utilizes the classification of storage structures based on the methodology outlined in Gammer et al. (2011). Several methods ex to calculate storage capacity. The storage capacity may in general terms be described as the pore volume of the aquifer in the storage assessment unit region multiplied with the storage efficiency factor (fraction of pore space where CO₂ “can” be injected). In the CCUS ZEN project, the capacity formulas Vangkilde-Pedersen et al. (2009) have been used:where: MCO₂ = calculated estimate storage capacity (in kg), A = considered area (regional or trap aquifer) (in m2), h = average thickness of the regional or trap aquifer suitable for CO₂ storage (in m), NG = average net to gross ratio of regional and trap aquifer (in %). This factor represents all the formation irregularities within the bulk volume, Φ = average reservoir porosity of the effectively porous rocks in the regional or trap aquifer (in %), ρCO₂ = CO₂ density at reservoir conditions (in kg/m³) and S_eff is storage efficiency factor (in %).

The screening of potential storage sites in the two geographical regions is carried out based on publicly available data from projects such as GESTCO, GeoCapacity (e.g., Vangkilde-Pedersen et al., 2009), CO2STOP (e.g., Poulsen et al., 2014), NORDICCS (e.g., Anthonsen et al., 2014a; Lothe et al., 2016), Strategy CCUS (e.g., Veloso, 2021), PilotSTRATEGY, and national projects. For each mapped storage site, information is gathered about the type of reservoir (deep saline aquifer or depleted hydrocarbon field), the onshore or offshore location, the capacity of the reservoir (mean value), and the Storage Readiness Level (SRL) indicating the maturity of the capacity evaluation based on Akhurst et al. (2021). Detailed description of the use of attribute names and data listed is defined in Tables 2, 3.

2.4 Mapping of utilization

Carbon Capture and Utilization includes many technologies that can capture CO₂ directly from the air or from industrial facilities. These technologies utilize CO2 as feedstocks to produce products like chemicals, fuels, and materials. Further details and descriptions of various types of CCU technologies can be found in IEA (2019), Chavez and Partenie (2020), and NASEM (2019). The primary source for the high-level screening of utilization is the CO₂ Value European database on CCU, which has been developed through previous EU projects like SCOT and IMPACTS9. This database contains approximately 250 ongoing and upcoming projects at different Technology Readiness Level (TRL; more details are listed in Ringstad et al. (2023).

3 Results of the high-level screening mapping

Figure 3 shows the results of the high-level screening of the Baltic and Mediterranean regions, highlighting marked emission sources and storage sites. The number of facilities and CO₂ emission sources varies significantly between countries, including significant emitters in both regions (Table 4). Large clusters of emitters are found in Poland and Germany in the Baltic region, as well as in Italy and Turkey in the Mediterranean Sea region. A comparison of the summarized numbers for the two regions reveals that the number of facilities and the annual CO₂ emissions are in the same range, with around 800 facilities and approximately 700 Mtpa (million tons per annum) in emissions. In the Baltic Sea region, large deep saline aquifers with significant storage capacities are mapped for Denmark, totalling 16,042 Mt (note that depleted hydrocarbon fields are excluded from this total), and for Poland, which has a storage capacity of 8,885 Mt, including both aquifers and hydrocarbon fields. In the southern region, Spain, Italy, and Greece demonstrate significant storage capacities, ranging from approximately 3.1–4.8 Gt, as illustrated in Table 5. Overall, the Baltic Sea region has three times more mapped storage capacities than the Mediterranean Sea region, with 33 Mt compared to 13.5 Mt, as shown in Table 5.

FIGURE 3

3.1 Identification of promising CCUS value chains

After the first screening of the mapped information, several emission clusters were identified, as well as storage options, and possible transport and intermediate storage solutions. Eight CCUS value chains were defined: four in the Baltic region and four in the Mediterranean region. This was based on a sink-source matching approach that considered estimated captured volumes and potential storage capacities. Value chains definition also handles transport scenarios and utilization projects (Figure 4, see also (Gravaud et al., 2024; Gravaud et al., 2025).

FIGURE 4

4 Example of a CCUS value chain; the Italian-Greece scenario

CCS projects and storage sites have been planned and evaluated in Italy for the past few decades; however, none have been carried out at full scale. The Brindisi CCS Project in southern Italy was evaluated by Enel and ENI using post-combustion technology, but the project was halted in 2016. The first CCS Hub in Italy, the Ravenna Carbon Capture and Storage (CCS) project, located in northeast Italy, started to inject in 2024, with Eni and Snam as operators (Figure 5). For phase 1, 25,000 tons of CO2 emitted from Eni’s natural gas treatment plant in Casalbosetti, Ravenna, are transported by pipeline and stored offshore Ravenna in a depleted gas field, with a potential impact of 10 Mtpa by 2030. Given that the Ravenna CCS project is ongoing in northern Italy, we will focus on mapping the potential CCUS value chain in southern Italy. In this article, we will further explore the Bradanica storage site onshore, southwest of Taranto (Figure 5).

FIGURE 5

4.1 Storage site

There are several potential CO₂ storage sites in Italy, both onshore and offshore, that have been mapped in the last decade (Donda et al., 2011; Civile et al., 2013; Barison et al., 2023). The CCUS ZEN project primarily had access to onshore site information as shown in Figure 6. Focusing on the southern part of Italy, where there are also large CO₂ emitters, the Bradanica site, situated close to Taranto city, could be a possible storage site. The potential storage reservoir consists of Late Pliocene sands and silty sands with marl and conglomerates in places, pinching out towards the eastern carbonate platform (Donda et al., 2011). These deposits have been interpreted as basin floor sandstone lobes (Patacca and Scandone, 2001), where flexure deformation occurred during the Plio-Pleistocene. The reservoir unit is locally more than 800 m thick, with an effective thickness of 650 m. The assumed caprock, clay and silty clay deposited from Late Pliocene are more than 1,500 m thick in some areas (Donda et al., 2011). From the CO2 storage capacity estimates in Donda et al. (2011), the reservoir has a storage capacity of 344 Mt, assuming an efficiency of 1%. If assuming a storage efficiency of 4%, 1,376 Mt can be stored, assuming a porosity value of 25% (Table 6).

FIGURE 6

4.2 Emission sources

In the southern part of Italy, we have identified several large CO₂ emitter hubs (Figure 5). The ones situated the closest to the possible storage site are the Taranto cluster and the Brindisi cluster.

Taranto is a coastal city in Apulia, southern Italy with one of the largest steel plants in Europe. The ArcelorMittal (Ilva steelworks) is one of the largest point emitters in Italy. The numbers listed in this report show 5.2 Mtpa of CO₂, while unofficial calculations, including the two thermoelectric power plans, sum up to around 10 Mtpa of CO₂ (based on the Environmental Declaration verified by EMAS in 2016). Thus, by only including official numbers, there are several emitters in the area, e.g., three refineries and one power plant, that are also to be part of a CCS hub (see Table 7). Figure 7 shows a pie chart for Taranto cluster, including also the two smallest emitters. The Taranto cluster then sums up to 12.4 Mtpa with the main sources from iron and steel plan, power, and refineries.

FIGURE 7

Thus, based on the IEA (2020) report and our own work, we assume that not all CO₂ emitted will be stored in the underground. We assume that the percentage of captured CO₂ varies by industry sector. We have used the same cut off, with the same reasoning as described more in detail in Shogenova et al. (2024a), for the Mediterranean value chain. A summary of the assumptions made is presented in Table 7. Table 8 shows the summary emissions for the different clusters in Southern Italy and Greece, respectively. Even with a large cut off, for instance, for the iron and steel industry and power, there are still large emissions, specially from southern Italy, but also from the Athens emission hub.

5 Discussion

The European Union and the United Kingdom are major energy consumers and CO₂ emitters, accounting for 12% of global emissions. The EU announced the Green Deal in 2019 to establish a roadmap for reducing emissions by at least 55% by 2030 and achieving zero emissions by 2050 (European Commission, 2019). Carbon capture and storage can be an important technology to contribute to fulfilling this ambition. In this article, we present a high-level CCUS value screening workflow and emphasize the main components needed in such a screening and workflow (Figure 2). The workflow has been tested in two regions in Europe that are less mature in terms of CCS: the Baltic and Mediterranean regions, with a more detailed case study presented for Italy-Greece. We will discuss several challenges in mapping a CCUS value chain, starting with the identification of emitters.

One of the results from the high-level CCUS screening in the two regions is that the number of emitters and the volume of emissions are in the same range for the Baltic and Mediterranean regions, with between 800–875 facilities and emissions approximately 700 Mtpa. For storage capacity, there are larger differences, with three times larger storage capacities mapped in the Baltic region compared to the Mediterranean region. One reason for this, is the easier access to data for the CCUS ZEN project in the Baltic region. More data has been made available in the Baltic over the last 3 decades. In the Mediterranean Sea, we did not have access to data for offshore France, we had little information from Italy and insufficient data available for the Castellon storage site in Spain, owned by the REPSOL oil company, which is currently planning detailed exploration for CO₂ storage in the TarraCO₂ project.

Reducing uncertainty in storage capacity, storage injectivity, and the longevity of a storage site is important. One major bottleneck at present is the lack of open geological datasets, including both 2D and 3D seismic datasets, and/or data from wells for potential storage formations. The underlying datasets needed, such as interpreted 2D seismic or 3D seismic data from existing wells, geological models, and/or reservoir models, are seldom publicly available. Scarce data coverage poses a major challenge in many regions, and in the CCUS ZEN project, the mapping of storage sites heavily relied on previous research projects. Since the screening of potential storage sites was based on publicly available data, it resulted in varying mapping coverage.

Another challenge related to mapping storage sites is the capacity of these potential storage locations. Indeed, databases present many sites with insufficient storage capacity for an operational CCS project to take place. For example, in Southern France, existing capacity data are on the order of a few tens of Mt, or even smaller, per site. Consequently, it is challenging to find sufficient storage capacity for the identified emission clusters and to build large-scale value chains. This is also a reason why transnational scenarios were developed. Finland lacks any storage potential, as it only has bedrock, and therefore the selected value chain suggested in CCUS ZEN involves pipeline or ship transport from Helsinki, Finland, to Rødby, a storage site in Denmark (Gravaud et al., 2024). Sweden has sedimentary deposits in the Baltic Sea, such as the Cambrian Faludden Formation, but with low storage potential, e.g., dipping aquifers with small natural closures (e.g., Lothe et al., 2016). However, the structures continue southwards on the Polish side and may serve as a potential storage structure.

For emission sources, there are complexities in deciding which industrial sites should be prioritized for CCS. The emission sources are subdivided based on the type of industry, varying from refineries, chemicals, power, hydrogen, energy from waste, cement, paper and pulp, iron and steel, and others. For some industries, CCS is the obvious option to reduce emissions (e.g., cement industry), while in other cases, CCS may be one of several options (with some form of electrification often being another). The level of CO₂ emissions in the future and the longevity of an industrial plant can also be factors in considering the deployment of CCS. However, information on this is difficult to obtain. It can be commercially sensitive, and there may also be political considerations that are hard to assess. For this reason, in this high-level screening, only the current emission levels from different industries are considered.

When choosing the emitter hub, several factors were evaluated. The type of industry, the number of emission sources, and, importantly, the location are very important factors. If there are several large industry clusters that can share common infrastructure, such as pipelines and/or buffer storage and/or ship transport, this can be crucial for building out an emission hub. In addition, the possibility of sharing a storage site would be beneficial for the emitters and for the owner of the storage site. The possible choice of storage sites are very much dependent on the transport infrastructure needed and the possible costs. In a high-level screening, only different options with distance in kilometres are shown.

For CO₂ emitters, a hub structure is attractive (Wang, 2024) to reduce the risk for each industry actor. A hub structure also minimizes the risk that transport, and storage infrastructure will be underutilized. A hub with more emitters will be less dependent on the emissions of a single industrial site for maintaining a high degree of utilization. In the screening, the total emissions amount of the clusters and the storage capacities are considered. However, it is recognized that actual total CO₂ emission volumes should be treated with caution. On one hand, the total amount of the clusters’ emissions does not exactly represent the amount of captured CO₂ but rather a maximum, as not 100% of the emissions would necessarily be captured. For some industries, transitioning to renewables or biogenic feedstocks may be more attractive and easier to implement.

In the example from Southern Italy, the high-level mapping for the entire CCUS value chain is essential to evaluate obstacles. Currently, Ravenna CCS has already started to inject CO₂ in their hub, and significant efforts are being made in Greece to clarify the offshore site Prinos for CO₂ storage (Koukouzas et al., 2009). However, as we see from the CO₂ emission hubs, there are potentially several emitter hubs in Southern Italy, where CO₂ can be transported via pipelines to the onshore Bradanica storage site. The storage capacity is around 344 Mt, assuming a storage efficiency of 1%, while using a storage efficiency of 4% results in around 1,276 Mt CO₂. Assuming an injection rate of 2 Mtpa in two wells, the storage site could be used for a minimum of 172 years. If we are less conservative, assuming a storage efficiency of 2%, the site could store for hundreds of years. Most likely, more injection wells could be an option, but to resolve this and de-risk the storage site, detailed reservoir modelling should be carried out. To develop a high-level value chain, all present and future stakeholders along the value chain need to be informed and aligned. Several key actors and driving forces will shape CCUS value chains, and these should be involved in the workflow. There is a strong interdependency among stakeholders with different interests, from industry emitters to transport and storage owners. To reduce risks, both economically and in terms of time spent, partnerships (or collaboration between stakeholders) across the value chain should be established.

Non-technical parameters influencing CCUS value chain developments include social, political, regulatory aspects, as well as economics, monitoring, reporting and verification and contracting. Communication with regulators, local public and non-governmental organisations and rising their awareness are always needed, but it is a time-consuming process (Honegger et al., 2024).

The export of CO₂ to offshore storage sites needs CO₂ storage regulations to be implemented internationally; (London Protocol (LP) 2009 Amendment to article 6, or/and its Provisional Application) and regionally (Helsinki Convention in the Baltic (HELCOM) and Barcelona Convention in the Mediterranean region), in addition to national regulations and permits needed for CO₂ storage both in onshore and offshore sites. At the present time LP 2009 Amendment to article 6 is implemented only in some studied countries of the Baltic Sea region (Denmark, Finland, Sweden and Estonia - among 13 countries implemented it in total). Denmark, Finland and Sweden are among nine countries in total which deposited declaration to allow for the Provisional Application of the 2009 amendment to article 6 of the LP. These regulations are not yet implemented in the Mediterranean Sea region, although there are some plans of Italy to do this including cooperation with France and Greece for bilateral agreements (IMO, 2025; Shogenova et al., 2024b).

The CO₂ storage is banned in the Baltic Sea now, according to the HELCOM, but The HELCOM recently decided to prepare in 2025–2026 the EIA (Environmental Impact Assessment) for CO₂ storage under the seabed in the Baltic Sea (information from personal communication of authors with national ministries). According to the initial Protocol of the Barcelona Convention CO₂ storage is permitted in the Mediterranean Sea. Public acceptance of CCUS technology in the studied regions is from low to medium with higher number of „medium” countries in the Baltics (Honegger et al., 2024).

The national regulations in the regions are developed in different directions. In the Baltic Sea Region, there are positive examples of Poland recently permitted CO₂ storage offshore and already prepared permitting regulations for onshore storage (to be published soon), and Latvia working in 2025 on CCS regulations towards its full implementation and possible permitting of CO₂ storage.

However, there is a negative example in the neighbouring Lithuania, which has banned any CO₂ injection since 2020, after CO₂ storage was initially permitted after full implementation of EU CCS Directive in 2011–2012 (Shogenova et al., 2013; Shogenova et al., 2021). These examples are clear signs of the increasing public awareness and acceptance of the technology in Poland and Latvia and low public acceptance in Lithuania. The Nordic countries are good examples of the positive influence of the non-technical issues, including policies and national financial support, on fast development of the CCUS technology, especially successful in Denmark with large numbers of very good storage sites and significant storage capacity.

6 Summary

The CCUS technical value chain screening involved mapping CO₂ emitters, infrastructure, storage sites, and utilization options using an open geographical information system. Emission sources were mapped to identify CO₂ capture sites, focusing on clusters for efficient transport to storage in the Baltic and Mediterranean regions. Data from the EU Emissions Trading System and the European Pollutant Release and Transfer Register were used for this mapping.

Existing and future CO₂ transport infrastructure was evaluated, including pipelines and shipping options, with a focus on combining methods for efficiency and compliance with regulations. Potential storage sites were categorized into saline aquifers and depleted reservoirs, with capacity estimates based on previous studies. The screening considered various geological data sources. CCU technologies were explored, utilizing CO₂ for producing chemicals and fuels, with data sourced from the CO₂ Value European database.

The screening revealed significant emitters in both regions, with around 800–875 facilities in each region emitting approximately 700 Mtpa. The Baltic region had larger mapped storage capacities than the Mediterranean. Eight CCUS value chains were developed based on emitter clusters and storage options, with a focus on transport scenarios.

7 Conclusions and recommendations

References

• 1

  Akhurst M. Kirk K. Neele F. Grimstad A. Bentham M. Bergmo P. (2021). Storage Readiness Levels: communicating the maturity of site technical understanding, permitting and planning needed for storage operations using CO₂. Int. J. Greenh. Gas Control110, 103402. 10.1016/j.ijggc.2021.103402

  • CrossRef
  • Google Scholar

• 2

  Anthonsen K. L. Aagaard P. Bergmo P. E. Gislason S. R. Lothe A. E. Mortensen G. M. et al (2014a). Characterisation and selection of the most prospective CO₂ storage sites in the Nordic region. Energy Procedia63, 4884–4489. 10.1016/j.egypro.2014.11.519

  • CrossRef
  • Google Scholar

• 3

  Anthonsen K. L. Bernstone C. Feldrappe H. (2014b). Screening for CO2 storage sites in southeast North Sea and southwest Baltic Sea. Energy Procedia63 (2014), 5083–5092. 10.1016/j.egypro.2014.11.538

  • CrossRef
  • Google Scholar

• 4

  Barison E. Donda F. Merson B. Le Gallo Y. Reveillere A. (2023). An insight into underground hydrogen storage in Italy. Sustainability15, 6886. 10.3390/su15086886

  • CrossRef
  • Google Scholar

• 5

  Bas D. Akpulat O. (2019). Technical assistance for developed analytical basis for formulating Strategies and actions towards low carbon development – Turkey capacity report 2019. EuropeAid/136032/IH/SER/TR.

  • Google Scholar

• 6

  Chavez E. Partenie O. (2020). Global CCU infrastructure market assessment, ECCSELRATE, 13. Deliverable D1.3.

  • Google Scholar

• 7

  Civile D. Zecchin M. Forlin E. Donda F. Volpi V. Merson B. et al (2013). CO2 geological storage in the Italian carbonate successions. Int. J. Greenh. Gas Control19, 101–116. 10.1016/j.ijggc.2013.08.010

  • CrossRef
  • Google Scholar

• 8

  Donda F. Volpi V. Persoglia S. Parushev D. (2011). CO2 storage potential of deep saline aquifers: the case of Italy. Int. J. Greenh. Gas Control, 327–335. 10.1016/j.ijggc.2010.08.009

  • CrossRef
  • Google Scholar

• 9

  European Commission (2019). A European green deal. Available online at: https://ec.europa.eu/info/strategy/priorities-2019-2024/european-green-deal_en.

  • Google Scholar

• 10

  European Commission (2024). Communication from the commission to the european parliament, the council, the european economic and social committee and the committee of the regions towards an ambitious Industrial Carbon Management for the EU. (COM/2024/62).

  • Google Scholar

• 11

  Gammer D. Green A. Holloway S. Smith G. (2011). “The energy technologies institute's UK CO₂ storage appraisal project (UKSAP),” in SPE Offshore Europe Oil and Gas Conference and Exhibition, Aberdeen, UK, 6–8 September 2011. SPE number 148426.

  • Google Scholar

• 12

  Gravaud I. Shogenova A. Shogenov K. Sousa L. H. Wójcicki A. Lothe A. E. et al (2024). Deliverable 1.2 Identification of promising CCUS value chains in the two ZEN regions for further analyses in WP3. Open report in EU Horizon Europe CCUS ZEN. Project 101075693.

  • Google Scholar

• 13

  Gravaud I. Lopez A. Koumentis I. Lothe A. E. Shogenova A. Bouvier L. et al (2025). Developing CCUS in Mediterranean region – technical evaluation of promising value chains. Submitted to International Greenhouse Gas Control.

  • Google Scholar

• 14

  Hjelm L. Anthonsen K. L. Dideriksen K. Nielsen C. M. Nielsen L. H. Mathiesen A. (2020). Evaluation of the CO2 storage potential in Denmark (GEUS rapport 2020/46).

  • Google Scholar

• 15

  Honegger M. Oh S. Schmitt F. Poralla M. Ombudstvedt I. Ostgaard L. et al (2024). “Making CCU and CCS hubs and clusters happen: overcoming non-technical challenges,” in Perspectives climate research on behalf of the CCUS ZEN project, D2.3 of CCUS ZEN project (Freiburg i.B., Germany), 70.

  • Google Scholar

• 16

  IEA (2019). Putting CO₂ to use: creating value from emissions, 86.

  • Google Scholar

• 17

  IEA (2020). CCUS in clean energy transitions. Paris: IEA. Available online at: https://www.iea.org/reports/ccus-in-clean-energy-transitions,Licence:CCBY4.0.

  • Google Scholar

• 18

  IMO (2025). Status of IMO treaties: comprehensive information on the status of multilateral Conventions and instruments in respect of which the International Maritime Organization or its Secretary-General performs depositary or other functions, 20 June (2025). Available online at: https://wwwcdn.imo.org/localresources/en/About/Conventions/StatusOfConventions/Status%202025.pdf.

  • Google Scholar

• 19

  IPCC (2006). in IPCC guidelines for national greenhouse gas inventories, prepared by the national greenhouse gas inventories programme. Editors EgglestonH. S.BuendiaL.MiwaK.NgaraT.TanabeK. (Japan: IGES).

  • Google Scholar

• 20

  Jakobsen J. P. Brunsvold A. (2011). Development of scenarios for carbon capture and storage ECCO - European value chain for CO2. Energy Procedia4, 2677–2684. 10.1016/j.egypro.2011.02.168

  • CrossRef
  • Google Scholar

• 21

  Kjärstad J. Johnsson F. (2009). Ramp-up of large-scale CCS infrastructure in Europe. Energy Procedia2009, 4201–4208. 10.1016/j.egypro.2009.02.230

  • CrossRef
  • Google Scholar

• 22

  Koukouzas N. Ziogou F. Gemeni V. (2009). Preliminary assessment of CO2 geological storage opportunities in Greece. Int. J. Greenh. Gas Control3, 502–513. 10.1016/j.ijggc.2008.10.005

  • CrossRef
  • Google Scholar

• 23

  Koukouzas N. Tyrologou P. Karapanos D. Carneiro J. Pereira P. de Mesquita Lobo Veloso F. et al (2021). Carbon capture, utilisation and storage as a defence tool against climate change: current developments in west Macedonia (Greece). Energies14 (11), 3321. 10.3390/en14113321

  • CrossRef
  • Google Scholar

• 24

  Lothe A. E. Bergmo P. E. S. Emmel B. U. Mortensen G. M. (2016). “CO₂ storage capacity estimates for a Norwegian and a Swedish aquifer using different approaches - from theoretical volumes, basin modelling to reservoir models,” in Geologic carbon sequestration: understanding reservoir concepts. Editor SinghT. N. (Springer International Publishing), 98–117.

  • Google Scholar

• 25

  Lothe A. E. Gravaud I. Falck da Silva E. Skagestad R. Shogenova A. Shogenov K. et al (2025). Deliverable 1.3 A framework for regional high-level technical screening of promising CCUS value chains. Open report in EU Horizon Europe CCUS ZEN. Project 101075693.

  • Google Scholar

• 26

  Mortensen G. M. Sopher D. (2021). Rapportering av regeringsuppdrag. Geologisk lagring av koldioxid i Sverige och i grannländer - status och utveckling 2021. Swedish: Sveriges geologiska undersökning.

  • Google Scholar

• 27

  NASEM (2019). Gaseous carbon waste stream utilization – status and research needs.

  • Google Scholar

• 28

  Patacca E. Scandone P. (2001). “Late thrust propagation and sedimentary response in the thrust-bet-foredeep system of the Southern Apennines (Pliocene-Pleistocene),” in Anatomy of an Oregon: the apeninnes and adjacent mediterranean basins. Editors VaiG. G.MariniI. P. (Kluwer Academic Publishers), 401–440.

  • Google Scholar

• 29

  Poulsen N. Holloway S. Neele F. Smith N. A. Kirk K. (2014). CO2STOP final report. Assessment of CO₂ storage potential in Europe 2014. Available online at: https://energy.ec.europa.eu/publications/assessment-co2-storage-potential-europe-co2stop_en.

  • Google Scholar

• 30

  Ringstad C. Falck da Silva E. Skagestad R. Heyn R. Biragnet C. Frykman P. et al (2023). Deliverable 1.1 High-level regional mapping of CO2 emission sources, utilization industry and infrastructure in the Baltic Sea and Mediterranean Sea regions. Open report in EU Horizon Europe CCUS ZEN. Project 101075693.

  • Google Scholar

• 31

  Shogenov K. Shogenova A. Vizika-Kavvadias O. (2013a). “Petrophysical properties and capacity of prospective for CO2 geological storage Baltic offshore and onshore structures,” in Energy procedia. (5036−5045) (Elsevier). 10.1016/j.egypro.2013.06.417

  • CrossRef
  • Google Scholar

• 32

  Shogenov K. Shogenova A. Vizika-Kavvadias O. (2013b). Potential structures for CO2 geological storage in the Baltic Sea: case study offshore Latvia. Bull. Geol. Soc. Finl.85 (1), 65–81. 10.17741/bgsf/85.1.005

  • CrossRef
  • Google Scholar

• 33

  Shogenova A. Sliaupa S. Vaher R. Shogenov K. Pomeranceva R. (2009). The Baltic Basin: structure, properties of reservoir rocks and capacity for geological storage of CO2. Est. J. Earth Sci.58 (4), 259–267. 10.3176/earth.2009.4.04

  • CrossRef
  • Google Scholar

• 34

  Shogenova A. Piessens K. Ivask J. Shogenov K. Martínez R. Flornes K. et al (2013). CCS Directive transposition into national laws in Europe: progress and problems by the end of 2011. Energy Procedia37, 7723–7731. 10.1016/j.egypro.2013.06.718

  • CrossRef
  • Google Scholar

• 35

  Shogenova A. Nordbäck N. Sopher D. Shogenov K. Niemi A. Juhlin C. et al (2021). “Carbon neutral baltic Sea Region by 2050: myth or reality?,” in 15th international conference on greenhouse gas control technologies, GHGT-15, 15-18 march 2021, abu dhabi, UAE. Elsevier, 1–12. SSRN. 10.2139/ssrn.3817722

  • CrossRef
  • Google Scholar

• 36

  Shogenova A. Shogenov K. Sousa L. H. Bonto M. Gravaud I. Lopez A. et al (2024a). Deliverable 3.1 CCUS value chains for the two CCUS ZEN regions selected for further development in WP4. Open report in EU Horizon Europe CCUS ZEN. Project 101075693.

  • Google Scholar

• 37

  Shogenova A. Shogenov K. Fantini M. Ferrari K. Guasti E. Martinelli F. et al (2024b). “Regulatory and political readiness of southern Europe for industrial implementation of CCUS technology: a case study from Italy and Greece,” in Proceedings of the 17th Greenhouse Gas Control Technologies Conference (GHGT-17) 20–24 October 2024. 10.2139/ssrn.5061103

  • CrossRef
  • Google Scholar

• 38

  Shogenova A. Shogenov K. Gravaud I. Sousa L. Wójcicki A. Lothe A. E. et al (2025). D3.3 A generic framework for selection of the most promising CCUS value chains. Open report in EU Horizon Europe CCUS ZEN. Project 101075693.

  • Google Scholar

• 39

  Simmer K. (2018). Estonian-Latvian transboundary carbon dioxide capture, transport and storage (CCS) scenario for the cement industry. Master Thesis: Tallinn University of Technology, 1–48.

  • Google Scholar

• 40

  Šliaupiene R. (2014). Prospects of CO₂ geological storage in the Baltic sedimentary basin. Vilnius: Summary of doctoral dissertation, 38. Available at: https://epublications.vu.lt/object/elaba:2176185/index.html.

  • Google Scholar

• 41

  Šliaupienė R. Šliaupa S. (2011). Prospects for CO₂ geological storage in deep saline aquifers of Lithuania and adjacent territories. Geologija53 (3), 121–133. Available at: https://mokslozurnalai.lmaleidykla.lt/publ/1392-110X/2011/3/Sliaupiene.pdf.

  • Google Scholar

• 42

  Tumara D. Uihlein A. Hidalgo Gonzalez I. (2024). Shaping the future CO2 transport network for Europe. Luxembourg: Publications Office of the European Union. 10.2760/582433,JRC136709

  • CrossRef
  • Google Scholar

• 43

  Vangkilde-Pedersen T. Anthonsen K. Smith N. Kirk K. Van der Meer B. Le Gallo Y. et al (2009). Assessing European capacity for geological storage of carbon dioxide – the EU GeoCapacity project. Energy Procedia, 2663–2670. 10.1016/j.egypro.2009.02.034

  • CrossRef
  • Google Scholar

• 44

  Veloso F. M. L. (2021). Maturity level and confidence of storage capacities estimates in the promising regions, 125. EU H2020 STRATEGY CCUS Project 837754, Report.

  • Google Scholar

• 45

  Wang R. (2024). Status and perspectives on CCUS clusters and hubs. Unconv. Resour.4 (2024), 100065. 10.1016/j.uncres.2023.100065

  • CrossRef
  • Google Scholar

• 46

  Wójcicki A. Nagy S. Lubaś J. Chećko J. Tarkowski R. (2014). Assessment of formations and structures suitable for safe CO2 storage (in Poland) including the monitoring plans 2014. Available online at: https://skladowanie.pgi.gov.pl/twiki/pub/CO2/WebHome/seq-summ.pdf.

  • Google Scholar